This is a “Highly Recommended” climate solution based on its effectiveness, scalability, and evidence of impact.

Protect Peatlands

Submitted by Drawdown Admin on
Sector
FALO & Nature-Based Carbon Removal
Mode
Cut Emissions Remove Carbon
Cluster
Protect & Manage Ecosystems
Image
Peatland
Coming Soon
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Summary

The Protect Peatlands solution is defined as legally protecting peatland ecosystems through establishment of protected areas (PAs), which preserves stored carbon and ensures continued carbon sequestration by reducing degradation of the natural hydrology, soils, and/or vegetation. This solution focuses on non-coastal peatlands that have not yet been drained or otherwise severely degraded. Reducing emissions from degraded peatlands is addressed in the Restore Peatlands solution, and mangroves located on peat soils are addressed in the Protect Coastal Wetlands solution.

Extreme weather events
Income & work,Health
Nature protection,Water resources
Description for Social and Search
Protect Peatlands is a HIghly Recommended climate solution. Peatland soils accumulate huge amounts of carbon over centuries. Protecting Peatlands reduces disturbances that turn these powerful carbon sinks into major sources of GHG emissions.
Overview

Peatlands are diverse ecosystems characterized by waterlogged, carbon-rich peat soils consisting of partially decomposed dead plant material (Figure 1). They are degraded or destroyed through clearing of vegetation and drainage for agriculture, forestry, peat extraction, or other development. An estimated 600 Gt carbon (~2,200 Gt CO₂‑eq ) is stored in peatlands, twice as much as the carbon stock in all forest biomass (Yu et al., 2010; Pan et al., 2024). Because decomposition occurs very slowly under waterlogged conditions, large amounts of plant material have accumulated in a partially decomposed state over millennia. These carbon-rich ecosystems occupy only 3–4% of land area (Xu et al., 2018b; United Nations Environment Programme [UNEP], 2022). Their protection is both feasible due to their small area and highly impactful due to their carbon density.

INSERT FIGURE 1

When peatlands are drained or disturbed, the rate of carbon loss increases sharply as the accumulated organic matter begins decomposing (Figure 2). Removal of overlying vegetation produces additional GHG emissions while also slowing or stopping carbon uptake. Whereas emissions from vegetation removal occur rapidly following disturbance, peat decomposition and associated emissions can continue for centuries depending on environmental conditions and peat thickness. Peat decomposition after disturbance occurs faster in warmer climates because cold temperatures slow microbial activity. In this analysis, we evaluated tropical, subtropical, temperate, and boreal regions separately.

Figure 2. Greenhouse gas emissions and sequestration in intact peatlands (left) and a drained peatland (right). Intact peatlands are a net greenhouse gas sink, sequestering carbon in peat through photosynthesis but also emitting methane due to waterlogged soils. Drained peatlands are a greenhouse gas source, producing emissions from peat decomposition and drainage canals.

Diagram comparing healthy and degraded peatland

Source: Link to source: https://www.iucn-uk-peatlandprogramme.org/news/new-briefing-addresses-peatlands-and-methane-debate 

In addition to peat decomposition, biomass removal, and lost carbon sequestration, peatland disturbance impacts methane and nitrous oxide emissions and carbon loss through waterways (Figure 2; Intergovernmental Panel on Climate Change [IPCC], 2014; UNEP, 2022). Intact peatlands are a methane source because of methane-producing microbes, which thrive under waterlogged conditions. However, carbon uptake typically outweighs methane emissions. Leifield et al. (2019) found that intact peatlands are a net carbon sink of 0.77 ± 0.15 t CO₂‑eq /ha/yr in temperate and boreal regions and 1.65 ± 0.51 t CO₂‑eq /ha/yr in tropical regions after accounting for methane emissions. Peatland drainage reduces methane emissions from the peatland itself, but the drainage ditches can become potent methane sources (Evans et al., 2015; Peacock et al., 2021). Dissolved and particulate organic carbon also run off through drainage ditches, increasing CO₂ emissions in waterways from microbial activity and abiotic processes. Finally, rates of nitrous oxide emissions increase following drainage as the nitrogen stored in the peat becomes available to microbes. 

Patterns of ongoing peatland drainage are poorly understood at the global scale, but rates of ecosystem disturbance are generally lower in PAs and on Indigenous peoples’ lands than outside of them (Li et al., 2024b; Wolf et al., 2021; Sze et al., 2021). The International Union for Conservation of Nature and Natural Resources (IUCN) defines six levels of PAs that vary in their allowed uses, ranging from strict wilderness preserves to sustainable use areas that allow for some extraction of natural resources. All PA levels were included in this analysis (UNEP World Conservation Monitoring Center [UNEP-WCMC] and IUCN, 2024). Due to compounding uncertainties in the distributions of peatlands and Indigenous peoples’ lands, which have not yet been comprehensively mapped, and unknown rates of peatland degradation within Indigenous people’s lands, peatlands within Indigenous peoples’ lands were excluded from the tables but are discussed in the text (Garnett et al., 2018; UNEP-WCMC and IUCN, 2024). 

Adams, V. M., Iacona, G. D., & Possingham, H. P. (2019). Weighing the benefits of expanding protected areas versus managing existing ones. Nature Sustainability, 2(5), 404–411. https://doi.org/10.1038/s41893-019-0275-5

Atkinson, C. L., & Alibašić, H. (2023). Prospects for Governance and Climate Change Resilience in Peatland Management in Indonesia. Sustainability, 15(3), Article 3. https://doi.org/10.3390/su15031839

Austin, K. G., Elsen, P. R., Coronado, E. N. H., DeGemmis, A., Gallego-Sala, A. V., Harris, L., Kretser, H. E., Melton, J. R., Murdiyarso, D., Sasmito, S. D., Swails, E., Wijaya, A., Winton, R. S., & Zarin, D. (2025). Mismatch between global importance of peatlands and the extent of their protection. Conservation Letters, 18(1), e13080. https://doi.org/10.1111/conl.13080

Barnes, M. D., Glew, L., Wyborn, C., & Craigie, I. D. (2018). Prevent perverse outcomes from global protected area policy. Nature Ecology & Evolution, 2(5), 759–762. https://doi.org/10.1038/s41559-018-0501-y

Bruner, A. G., Gullison, R. E., & Balmford, A. (2004). Financial costs and shortfalls of managing and expanding protected-area systems in developing countries. BioScience, 54(12), 1119–1126. https://doi.org/10.1641/0006-3568(2004)054[1119:FCASOM]2.0.CO;2

Conchedda, G., & Tubiello, F. N. (2020). Drainage of organic soils and GHG emissions: Validation with country data. Earth System Science Data, 12(4), 3113–3137. https://doi.org/10.5194/essd-12-3113-2020

Davidson, N. C. (2014). How much wetland has the world lost? Long-term and recent trends in global wetland area. Marine and Freshwater Research, 65(10), 934. https://doi.org/10.1071/MF14173

Deshmukh, C. S., Julius, D., Desai, A. R., Asyhari, A., Page, S. E., Nardi, N., Susanto, A. P., Nurholis, N., Hendrizal, M., Kurnianto, S., Suardiwerianto, Y., Salam, Y. W., Agus, F., Astiani, D., Sabiham, S., Gauci, V., & Evans, C. D. (2021). Conservation slows down emission increase from a tropical peatland in Indonesia. Nature Geoscience, 14(7), Article 7. https://doi.org/10.1038/s41561-021-00785-2

Dietrich, O., & Behrendt, A. (2022). Wet Grassland Sites with Shallow Groundwater Conditions: Effects on Local Meteorological Characteristics. Water, 14(21), Article 21. https://doi.org/10.3390/w14213560

Dinerstein, E., Joshi, A. R., Hahn, N. R., Lee, A. T. L., Vynne, C., Burkart, K., Asner, G. P., Beckham, C., Ceballos, G., Cuthbert, R., Dirzo, R., Fankem, O., Hertel, S., Li, B. V., Mellin, H., Pharand-Deschênes, F., Olson, D., Pandav, B., Peres, C. A., … Zolli, A. (2024). Conservation imperatives: Securing the last unprotected terrestrial sites harboring irreplaceable biodiversity. Frontiers in Science, 2. https://doi.org/10.3389/fsci.2024.1349350

Evers, S., Yule, C. M., Padfield, R., O’Reilly, P., & Varkkey, H. (2017). Keep wetlands wet: The myth of sustainable development of tropical peatlands – implications for policies and management. Global Change Biology, 23(2), 534–549. https://doi.org/10.1111/gcb.13422

Felipe Cadillo, M. M., & Bennett, A. (2024). Navigating socio-political threats to Amazonian peatland conservation: Insights from the Imiria Region, Peru. Sustainability, 16(16), Article 16. https://doi.org/10.3390/su16166967

Fluet-Chouinard, E., Stocker, B. D., Zhang, Z., Malhotra, A., Melton, J. R., Poulter, B., Kaplan, J. O., Goldewijk, K. K., Siebert, S., Minayeva, T., Hugelius, G., Joosten, H., Barthelmes, A., Prigent, C., Aires, F., Hoyt, A. M., Davidson, N., Finlayson, C. M., Lehner, B., … McIntyre, P. B. (2023). Extensive global wetland loss over the past three centuries. Nature, 614(7947), 281–286. https://doi.org/10.1038/s41586-022-05572-6

Fuller, C., Ondei, S., Brook, B. W., & Buettel, J. C. (2020). Protected-area planning in the Brazilian Amazon should prioritize additionality and permanence, not leakage mitigation. Biological Conservation, 248, 108673. https://doi.org/10.1016/j.biocon.2020.108673

Garnett, S. T., Burgess, N. D., Fa, J. E., Fernández-Llamazares, Á., Molnár, Z., Robinson, C. J., Watson, J. E. M., Zander, K. K., Austin, B., Brondizio, E. S., Collier, N. F., Duncan, T., Ellis, E., Geyle, H., Jackson, M. V., Jonas, H., Malmer, P., McGowan, B., Sivongxay, A., & Leiper, I. (2018). A spatial overview of the global importance of Indigenous lands for conservation. Nature Sustainability, 1(7), 369–374. https://doi.org/10.1038/s41893-018-0100-6

Girkin, N. T., & Davidson, S. J. (2024). Protect peatlands to achieve climate goals. Science, 383(6682), 490–490. https://doi.org/10.1126/science.adn4001

Girkin, N. T., Burgess, P. J., Cole, L., Cooper, H. V., Honorio Coronado, E., Davidson, S. J., Hannam, J., Harris, J., Holman, I., McCloskey, C. S., McKeown, M. M., Milner, A. M., Page, S., Smith, J., & Young, D. (2023). The three-peat challenge: Business as usual, responsible agriculture, and conservation and restoration as management trajectories in global peatlands. Carbon Management, 14(1), 2275578. https://doi.org/10.1080/17583004.2023.2275578

Goib, B. K., Fitriani, N., Wicaksono, S., & Chitra, J. (2018). Restoring peat, improving welfare, and empowering women: Can we have it all? https://wri-indonesia.org/en/insights/restoring-peat-improving-welfare-and-empowering-women-can-we-have-it-all

Goldstein, A., Turner, W. R., Spawn, S. A., Anderson-Teixeira, K. J., Cook-Patton, S., Fargione, J., Gibbs, H. K., Griscom, B., Hewson, J. H., Howard, J. F., Ledezma, J. C., Page, S., Koh, L. P., Rockström, J., Sanderman, J., & Hole, D. G. (2020). Protecting irrecoverable carbon in Earth’s ecosystems. Nature Climate Change, 10(4), 287–295. https://doi.org/10.1038/s41558-020-0738-8

Griscom, B. W., Adams, J., Ellis, P. W., Houghton, R. A., Lomax, G., Miteva, D. A., Schlesinger, W. H., Shoch, D., Siikamäki, J. V., Smith, P., Woodbury, P., Zganjar, C., Blackman, A., Campari, J., Conant, R. T., Delgado, C., Elias, P., Gopalakrishna, T., Hamsik, M. R., … Fargione, J. (2017). Natural climate solutions. Proceedings of the National Academy of Sciences, 114(44), 11645–11650. https://doi.org/10.1073/pnas.1710465114

Harris, L. I., Richardson, K., Bona, K. A., Davidson, S. J., Finkelstein, S. A., Garneau, M., McLaughlin, J., Nwaishi, F., Olefeldt, D., Packalen, M., Roulet, N. T., Southee, F. M., Strack, M., Webster, K. L., Wilkinson, S. L., & Ray, J. C. (2022). The essential carbon service provided by northern peatlands. Frontiers in Ecology and the Environment, 20(4), 222–230. https://doi.org/10.1002/fee.2437

Harrison, M. E., & Paoli, G. D. (2012). Managing the Risk of Biodiversity Leakage from Prioritising REDD+ in the Most Carbon-Rich Forests: The Case Study of Peat-Swamp Forests in Kalimantan, Indonesia. Tropical Conservation Science, 5(4), 426–433. https://doi.org/10.1177/194008291200500402

Hein, L., Spadaro, J. V., Ostro, B., Hammer, M., Sumarga, E., Salmayenti, R., Boer, R., Tata, H., Atmoko, D., & Castañeda, J.-P. (2022). The health impacts of Indonesian peatland fires. Environmental Health, 21(1), 62. https://doi.org/10.1186/s12940-022-00872-w

Helbig, M., Waddington, J. M., Alekseychik, P., Amiro, B., Aurela, M., Barr, A. G., Black, T. A., Carey, S. K., Chen, J., Chi, J., Desai, A. R., Dunn, A., Euskirchen, E. S., Flanagan, L. B., Friborg, T., Garneau, M., Grelle, A., Harder, S., Heliasz, M., … Schulze, C. (2020). The biophysical climate mitigation potential of boreal peatlands during the growing season. Environmental Research Letters, 15(10), 104004. https://doi.org/10.1088/1748-9326/abab34

Hugelius, G., Loisel, J., Chadburn, S., Jackson, R. B., Jones, M., MacDonald, G., Marushchak, M., Olefeldt, D., Packalen, M., Siewert, M. B., Treat, C., Turetsky, M., Voigt, C., & Yu, Z. (2020). Large stocks of peatland carbon and nitrogen are vulnerable to permafrost thaw. Proceedings of the National Academy of Sciences, 117(34), 20438–20446. https://doi.org/10.1073/pnas.1916387117

Humpenöder, F., Karstens, K., Lotze-Campen, H., Leifeld, J., Menichetti, L., Barthelmes, A., & Popp, A. (2020). Peatland protection and restoration are key for climate change mitigation. Environmental Research Letters, 15(10), 104093. https://doi.org/10.1088/1748-9326/abae2a

IPCC 2014, 2013 Supplement to the 2006 IPCC Guidelines for National Greenhouse Gas Inventories: Wetlands, Hiraishi, T., Krug, T., Tanabe, K., Srivastava, N., Baasansuren, J., Fukuda, M. and Troxler, T.G. (eds). Published: IPCC, Switzerland.

IUCN. Peatlands and Climate Change (IUCN Issues Briefs). (2021). Link to source: https://iucn.org/sites/default/files/2022-04/iucn_issues_brief_peatlands_and_climate_change_final_nov21.pdf

Jalilov, S.-M., Rochmayanto, Y., Hidayat, D. C., Raharjo, J. T., Mendham, D., & Langston, J. D. (2025). Unveiling economic dimensions of peatland restoration in Indonesia: A systematic literature review. Ecosystem Services, 71, 101693. https://doi.org/10.1016/j.ecoser.2024.101693

Jones, M. C., Harden, J., O’Donnell, J., Manies, K., Jorgenson, T., Treat, C., & Ewing, S. (2017). Rapid carbon loss and slow recovery following permafrost thaw in boreal peatlands. Global Change Biology, 23(3), 1109–1127. https://doi.org/10.1111/gcb.13403

Kiely, L., Spracklen, D. V., Arnold, S. R., Papargyropoulou, E., Conibear, L., Wiedinmyer, C., Knote, C., & Adrianto, H. A. (2021). Assessing costs of Indonesian fires and the benefits of restoring peatland. Nature Communications, 12(1), 7044. https://doi.org/10.1038/s41467-021-27353-x

Konecny, K., Ballhorn, U., Navratil, P., Jubanski, J., Page, S. E., Tansey, K., Hooijer, A., Vernimmen, R., & Siegert, F. (2016). Variable carbon losses from recurrent fires in drained tropical peatlands. Global Change Biology, 22(4), 1469–1480. https://doi.org/10.1111/gcb.13186

Leifeld, J., & Menichetti, L. (2018). The underappreciated potential of peatlands in global climate change mitigation strategies. Nature Communications, 9(1), 1071. https://doi.org/10.1038/s41467-018-03406-6

Leifeld, J., Wüst-Galley, C., & Page, S. (2019). Intact and managed peatland soils as a source and sink of GHGs from 1850 to 2100. Nature Climate Change, 9(12), 945–947. https://doi.org/10.1038/s41558-019-0615-5

Li, B. V., Wu, S., Pimm, S. L., & Cui, J. (2024a). The synergy between protected area effectiveness and economic growth. Current Biology, 34(13), 2907-2920.e5. https://doi.org/10.1016/j.cub.2024.05.044

Li, G., Fang, C., Watson, J. E. M., Sun, S., Qi, W., Wang, Z., & Liu, J. (2024b). Mixed effectiveness of global protected areas in resisting habitat loss. Nature Communications, 15(1), 8389. https://doi.org/10.1038/s41467-024-52693-9

Loisel, J., Gallego-Sala, A. V., Amesbury, M. J., Magnan, G., Anshari, G., Beilman, D. W., Benavides, J. C., Blewett, J., Camill, P., Charman, D. J., Chawchai, S., Hedgpeth, A., Kleinen, T., Korhola, A., Large, D., Mansilla, C. A., Müller, J., van Bellen, S., West, J. B., … Wu, J. (2021). Expert assessment of future vulnerability of the global peatland carbon sink. Nature Climate Change, 11(1), 70–77. https://doi.org/10.1038/s41558-020-00944-0

Marlier, M. E., Liu, T., Yu, K., Buonocore, J. J., Koplitz, S. N., DeFries, R. S., Mickley, L. J., Jacob, D. J., Schwartz, J., Wardhana, B. S., & Myers, S. S. (2019). Fires, smoke exposure, and public health: An integrative framework to maximize health benefits from peatland restoration. GeoHealth, 3(7), 178–189. https://doi.org/10.1029/2019GH000191

Melton, J. R., Chan, E., Millard, K., Fortier, M., Winton, R. S., Martín-López, J. M., Cadillo-Quiroz, H., Kidd, D., & Verchot, L. V. (2022). A map of global peatland extent created using machine learning (Peat-ML). Geoscientific Model Development, 15(12), 4709–4738. https://doi.org/10.5194/gmd-15-4709-2022

Miettinen, J., Shi, C., & Liew, S. C. (2011). Deforestation rates in insular Southeast Asia between 2000 and 2010. Global Change Biology, 17(7), 2261–2270. https://doi.org/10.1111/j.1365-2486.2011.02398.x

Miettinen, J., Shi, C., & Liew, S. C. (2016). Land cover distribution in the peatlands of Peninsular Malaysia, Sumatra and Borneo in 2015 with changes since 1990. Global Ecology and Conservation, 6, 67–78. https://doi.org/10.1016/j.gecco.2016.02.004

Minasny, B., Adetsu, D. V., Aitkenhead, M., Artz, R. R. E., Baggaley, N., Barthelmes, A., Beucher, A., Caron, J., Conchedda, G., Connolly, J., Deragon, R., Evans, C., Fadnes, K., Fiantis, D., Gagkas, Z., Gilet, L., Gimona, A., Glatzel, S., Greve, M. H., … Zak, D. (2024). Mapping and monitoring peatland conditions from global to field scale. Biogeochemistry, 167(4), 383–425. https://doi.org/10.1007/s10533-023-01084-1

Minayeva, T. Yu., Bragg, O. M., & Sirin, A. A. (2017). Towards ecosystem-based restoration of peatland biodiversity. Mires and Peat, 19, 1–36. https://doi.org/10.19189/MaP.2013.OMB.150

Müller, J., & Joos, F. (2021). Committed and projected future changes in global peatlands – continued transient model simulations since the Last Glacial Maximum. Biogeosciences, 18(12), 3657–3687. https://doi.org/10.5194/bg-18-3657-2021

Nelson, K., Thompson, D., Hopkinson, C., Petrone, R., & Chasmer, L. (2021). Peatland-fire interactions: A review of wildland fire feedbacks and interactions in Canadian boreal peatlands. Science of The Total Environment, 769, 145212. https://doi.org/10.1016/j.scitotenv.2021.145212

Noon, M. L., Goldstein, A., Ledezma, J. C., Roehrdanz, P. R., Cook-Patton, S. C., Spawn-Lee, S. A., Wright, T. M., Gonzalez-Roglich, M., Hole, D. G., Rockström, J., & Turner, W. R. (2022). Mapping the irrecoverable carbon in Earth’s ecosystems. Nature Sustainability, 5(1), 37–46. https://doi.org/10.1038/s41893-021-00803-6

Pan, Y., Birdsey, R. A., Phillips, O. L., Houghton, R. A., Fang, J., Kauppi, P. E., Keith, H., Kurz, W. A., Ito, A., Lewis, S. L., Nabuurs, G.-J., Shvidenko, A., Hashimoto, S., Lerink, B., Schepaschenko, D., Castanho, A., & Murdiyarso, D. (2024). The enduring world forest carbon sink. Nature, 631(8021), 563–569. https://doi.org/10.1038/s41586-024-07602-x

Peacock, M., Audet, J., Bastviken, D., Futter, M. N., Gauci, V., Grinham, A., Harrison, J. A., Kent, M. S., Kosten, S., Lovelock, C. E., Veraart, A. J., & Evans, C. D. (2021). Global importance of methane emissions from drainage ditches and canals. Environmental Research Letters, 16(4), 044010. https://doi.org/10.1088/1748-9326/abeb36

Posa, M. R. C., Wijedasa, L. S., & Corlett, R. T. (2011). Biodiversity and conservation of tropical peat swamp forests. BioScience, 61(1), 49–57. https://doi.org/10.1525/bio.2011.61.1.10

Ritson, J. P., Bell, M., Brazier, R. E., Grand-Clement, E., Graham, N. J. D., Freeman, C., Smith, D., Templeton, M. R., & Clark, J. M. (2016). Managing peatland vegetation for drinking water treatment. Scientific Reports, 6(1), 36751. https://doi.org/10.1038/srep36751

Sasmito, S. D., Taillardat, P., Adinugroho, W. C., Krisnawati, H., Novita, N., Fatoyinbo, L., Friess, D. A., Page, S. E., Lovelock, C. E., Murdiyarso, D., Taylor, D., & Lupascu, M. (2025). Half of land use carbon emissions in Southeast Asia can be mitigated through peat swamp forest and mangrove conservation and restoration. Nature Communications, 16(1), 740. https://doi.org/10.1038/s41467-025-55892-0

Schulz, C., Martín Brañas, M., Núñez Pérez, C., Del Aguila Villacorta, M., Laurie, N., Lawson, I. T., & Roucoux, K. H. (2019). Uses, cultural significance, and management of peatlands in the Peruvian Amazon: Implications for conservation. Biological Conservation, 235, 189–198. https://doi.org/10.1016/j.biocon.2019.04.005

Spitzer, K., & Danks, H. V. (2006). Insect biodiversity of boreal peat bogs. Annual Review of Entomology, 51, 137–161. https://doi.org/10.1146/annurev.ento.51.110104.151036

Strack, M., Davidson, S. J., Hirano, T., & Dunn, C. (2022). The potential of peatlands as nature-based climate solutions. Current Climate Change Reports, 8(3), 71–82. https://doi.org/10.1007/s40641-022-00183-9

Suwarno, A., Hein, L., & Sumarga, E. (2016). Who benefits from ecosystem services? A case study for central Kalimantan, Indonesia. Environmental Management, 57(2), 331–344. https://doi.org/10.1007/s00267-015-0623-9

Syahza, A., Suswondo, Bakce, D., Nasrul, B., Irianti, W., & Irianti, M. (2020). Peatland policy and management strategy to support sustainable development in Indonesia. Journal of Physics: Conference Series, 1655, 012151. Link to source: https://doi.org/10.1088/1742-6596/1655/1/012151

Sze, J. S., Carrasco, L. R., Childs, D., & Edwards, D. P. (2021). Reduced deforestation and degradation in Indigenous Lands pan-tropically. Nature Sustainability, 5(2), 123–130. https://doi.org/10.1038/s41893-021-00815-2

Tan, Z. D., Lupascu, M., & Wijedasa, L. S. (2021). Paludiculture as a sustainable land use alternative for tropical peatlands: A review. Science of The Total Environment, 753, 142111. https://doi.org/10.1016/j.scitotenv.2020.142111

Thorburn, C. C., & Kull, C. A. (2015). Peatlands and plantations in Sumatra, Indonesia: Complex realities for resource governance, rural development and climate change mitigation. Asia Pacific Viewpoint, 56(1), 153–168. https://doi.org/10.1111/apv.12045

Thornton, S. A., Setiana, E., Yoyo, K., Dudin, Yulintine, Harrison, M. E., Page, S. E., & Upton, C. (2020). Towards biocultural approaches to peatland conservation: The case for fish and livelihoods in Indonesia. Environmental Science & Policy, 114, 341–351. https://doi.org/10.1016/j.envsci.2020.08.018

Turetsky, M. R., Benscoter, B., Page, S., Rein, G., van der Werf, G. R., & Watts, A. (2015). Global vulnerability of peatlands to fire and carbon loss. Nature Geoscience, 8(1), 11–14. https://doi.org/10.1038/ngeo2325

Uda, S. K., Hein, L., & Sumarga, E. (2017). Towards sustainable management of Indonesian tropical peatlands. Wetlands Ecology and Management, 25(6), 683–701. https://doi.org/10.1007/s11273-017-9544-0

Uda, S. K., Hein, L., & Atmoko, D. (2019). Assessing the health impacts of peatland fires: A case study for Central Kalimantan, Indonesia. Environmental Science and Pollution Research, 26(30), 31315–31327. https://doi.org/10.1007/s11356-019-06264-x

UNEP (2022). Global Peatlands Assessment – The State of the World’s Peatlands: Evidence for action toward the conservation, restoration, and sustainable management of peatlands. Main Report. Global Peatlands Initiative. United Nations Environment Programme, Nairobi.

UNEP-WCMC and IUCN. (2024). Protected Planet Report. UNEP-WCMC and IUCN. https://digitalreport.protectedplanet.net

Waldron, A., Adams, V., Allan, J., Arnell, A., Asner, G., Atkinson, S., Baccini, A., Baillie, J., Balmford, A., & Austin Beau, J. (2020). Protecting 30% of the planet for nature: Costs, benefits and economic implications. https://pure.iiasa.ac.at/id/eprint/16560/1/Waldron_Report_FINAL_sml.pdf

Williams, M., Reay, D., & Smith, P. (2023). Avoiding emissions versus creating sinks—Effectiveness and attractiveness to climate finance. Global Change Biology, 29(8), 2046–2049. https://doi.org/10.1111/gcb.16598

Wolf, C., Levi, T., Ripple, W. J., Zárrate-Charry, D. A., & Betts, M. G. (2021). A forest loss report card for the world’s protected areas. Nature Ecology & Evolution, 5(4), 520–529. https://doi.org/10.1038/s41559-021-01389-0

Worrall, F., Howden, N. J. K., Burt, T. P., Rico-Ramirez, M. A., & Kohler, T. (2022). Local climate impacts from ongoing restoration of a peatland. Hydrological Processes, 36(3), e14496. https://doi.org/10.1002/hyp.14496

Xu, J., Morris, P. J., Liu, J., & Holden, J. (2018a). Hotspots of peatland-derived potable water use identified by global analysis. Nature Sustainability, 1(5), 246–253. https://doi.org/10.1038/s41893-018-0064-6

Xu, J., Morris, P. J., Liu, J., & Holden, J. (2018b). PEATMAP: Refining estimates of global peatland distribution based on a meta-analysis. CATENA, 160, 134–140. https://doi.org/10.1016/j.catena.2017.09.010

Yu, Z., Loisel, J., Brosseau, D. P., Beilman, D. W., & Hunt, S. J. (2010). Global peatland dynamics since the Last Glacial Maximum. Geophysical Research Letters, 37(13). https://doi.org/10.1029/2010GL043584

Credits

Lead Fellow

Avery Driscoll

Contributors

Ruthie Burrows, Ph.D.

James Gerber, Ph.D.

Daniel Jasper

Alex Sweeney

Internal Reviewers

Aiyana Bodi

Hannah Henkin

Megan Matthews, Ph.D.

Ted Otte

Christina Swanson, Ph.D.

Paul West, Ph.D.

Effectiveness

We estimated that protecting a ha of peatland avoids 0.92–13.47 t CO₂‑eq /ha/yr, with substantially higher emissions reductions in subtropical and tropical regions and lower emissions reductions in boreal regions (100-yr GWP; Table 1a–d; Appendix). 

We estimated effectiveness as the avoided emissions attributable to the reduction in peatland loss conferred by protection (Equation 1). First, we calculated the biome-specific difference between the annual rate of peatland loss outside PAs (Peatland lossbaseline) versus inside PAs (Peatland lossprotected) (Appendix; Conchedda & Tubellio, 2020; Davidson et al., 2014; Miettinen et al., 2011; Miettinen et al., 2016; Uda et al., 2017, Wolf et al., 2021). We then multiplied the avoided peatland loss by the total emissions from one ha of drained peatland over 30 years. This is the sum of the total biomass carbon stock (Carbonbiomass), which degrades relatively quickly; 30 years of annual emissions from peat itself (Carbonflux); and 30 years of lost carbon sequestration potential, reflecting the carbon that would have been taken up by one ha of intact peatland in the absence of degradation (Carbonuptake) (IPCC 2014; UNEP, 2022). The carbon flux includes CO₂‑eq emissions from: 1) peat oxidation, 2) dissolved organic carbon loss through drainage, 3) the net change in on-field methane between undrained and drained states, 4) methane emissions from drainage ditches, and 5) on-field nitrous oxide emissions.

Equation 1. 

Effectiveness= (Peatland lossbaseline- Peatland lossprotected)* (Carbonbiomass + 30*Carbonflux + 30*Carbonuptake) 

Without rewetting, peat loss typically persists beyond 30 years and can continue for centuries (Leifield & Menichetti, 2018). Thus, this is a conservative estimate of peatland protection effectiveness that captures near-term impacts, aligns with the 30-yr cost amortization time frame, and is roughly consistent with commonly used 2050 targets. Using a longer time frame produces larger estimates of emissions from degraded peatlands and therefore higher effectiveness of peatland protection.

The effectiveness of peatland protection as defined here reflects only a small percentage of the carbon stored in peatlands because we account for the likelihood that the peatland would be destroyed without protection. Peatland protection is particularly impactful for peatlands at high risk of drainage.

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Table 1. Effectiveness of peatland protection at avoiding emissions and sequestering carbon. Regional differences in values are driven by variation in emissions factors and baseline rates of peatland drainage.

Unit: t CO₂‑eq , 100-yr basis/ha of peatland protected/yr

t CO₂‑eq (100-yr basis)/ha/yr 0.92

Unit: t CO₂‑eq , 100-yr basis/ha of peatland protected/yr

t CO₂‑eq (100-yr basis)/ha/yr 4.42

Unit: t CO₂‑eq , 100-yr basis/ha of peatland protected/yr

t CO₂‑eq (100-yr basis)/ha/yr 13.47

Unit: t CO₂‑eq , 100-yr basis/ha of peatland protected/yr

t CO₂‑eq (100-yr basis)/ha/yr 13.23
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Cost

We estimated that the net cost of peatland protection is approximately US$1.5/ha/yr, or $0.25/t CO₂‑eq avoided (Table 2). Data related to the costs of peatland protection are very limited. These estimates reflect global averages rather than regionally specific values, and rarely include data specific to peatlands. The costs of peatland protection include up-front costs of land acquisition and ongoing costs of management and enforcement. The market price of land reflects the opportunity cost of not using the land for other purposes, such as agriculture, forestry, peat extraction, or urban development. Protecting peatlands can also generate revenue through increased tourism. Costs and revenues are highly variable across regions, depending on the costs of land and enforcement and potential for tourism. 

Dienerstein et al. (2024) estimated the initial cost of establishing a protected area for 60 high-biodiversity ecoregions. Amongst the 33 regions that were likely to contain peatlands, the median acquisition cost was US$957/ha, which we amortized over 30 years. Costs of protected area maintenance were estimated at US$9–17/ha/yr (Bruner et al., 2004; Waldron et al., 2020), though these estimates were not specific to peatlands. Additionally, these estimates reflect the costs of effective enforcement and management, but many existing protected areas lack adequate funds for effective enforcement (Adams et al., 2019; Barnes et al., 2018; Burner et al., 2004). Waldron et al. (2020) estimated that, across all ecosystems, tourism revenues directly attributable to protected area establishment were US$43 ha/yr, not including downstream revenues from industries that benefit from increased tourism. Inclusion of a tourism multiplier would substantially increase the estimated economic benefits of peatland protection.

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Table 2. Cost per unit climate impact for peatland protection.

Unit: 2023 US$/t CO₂‑eq , 100-yr basis

median 0.25
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Learning Curve

A learning curve is defined here as falling costs with increased adoption. The costs of peatland protection do not fall with increasing adoption, so there is no learning curve for this solution.

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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as gradual, emergency brake, or delayed.

Protect Peatlands is an EMERGENCY BRAKE climate solution. It has the potential to deliver a more rapid impact than nominal and delayed solutions. Because emergency brake solutions can deliver their climate benefits quickly, they can help accelerate our efforts to address dangerous levels of climate change. For this reason, they are a high priority.

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Caveats

Permanence, or the durability of stored carbon, is a caveat for emissions avoidance through peatland protection that is not addressed in this analysis. Protected peatlands could be drained if legal protections are reversed or inadequately enforced, resulting in the loss of stored carbon. Additionally, fires on peatlands have become more frequent due to climate change (Turetsky et al., 2015; Loisel et al., 2021), and can produce very large emissions pulses (Konecny et al., 2016; Nelson et al., 2021). In boreal regions, permafrost thaw can trigger large, sustained carbon losses from previously frozen peat (Hugelius et al., 2020; Jones et al., 2017). In tropical regions, climate change-induced changes in precipitation can lower water tables in intact peatlands, increasing risks of peat loss and reducing sequestration potential (Deshmukh et al., 2021). 

Additionality, or the degree to which emissions reductions are above and beyond a baseline, is another important caveat for emissions avoidance through ecosystem protection (Atkinson & Alibašić, 2023; Fuller et al., 2020; Williams et al., 2023). In this analysis, additionality was addressed by using baseline rates of peatland degradation in calculating effectiveness. Evaluating additionality is challenging and remains an active area of research.

Finally, there are substantial uncertainties in the available data on peatland areas and distributions, peatland loss rates, the drivers of peatland loss, the extent and boundaries of PAs, and the efficacy of PAs at reducing peatland disturbance. Emissions dynamics on both intact and cleared peatlands are also uncertain, particularly under different land management practices and in the context of climate change.

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Current Adoption

Because peatlands are characterized by their soils rather than by overlying vegetation, they are difficult to map at the global scale (Minasny et al., 2024). Mapping peatlands remains an active area of research, and the adoption values presented here are uncertain. We estimated that 22.6 Mha of peatlands are located within strictly protected PAs (IUCN classes I or II), and 82.2 Mha are within other or unknown PA classes (Table 3a–e; UNEP, 2022; UNEP-WCMC & IUCN, 2024), representing 22% of total global peatland area (482 Mha). Because of data limitations, we did not include Indigenous peoples’ lands in subsequent analyses despite their conservation benefits. There are an additional 186 Mha of peatlands within Indigenous peoples’ lands that are not also classified PAs, with a large majority (155 Mha) located in boreal regions (Table 3; Garnett et al., 2018; UNEP, 2022).

Given the uncertainty in the global extent of peatlands, estimates of peatland protection vary. The Global Peatlands Assessment estimated that 19% (90.7 Mha) of peatlands are protected (UNEP, 2022), with large regional variations ranging from 35% of peatlands protected in Africa to only 10% in Asia. Using a peatland map from Melton et al. (2012), Austin et al. (2025) estimated that 17% of global peatlands are within PAs, and an additional 27% are located in Indigenous peoples’ lands (excluding Indigenous peoples’ lands in Canada covering large peatland areas).

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Table 3. Current peatland area under protection by biome (circa 2023). Estimates are provided for two different forms of protection: “strict” protection, including IUCN classes I and II, and “nonstrict” protection, including all other IUCN classes. Regional values may not sum to global totals due to rounding.

Unit: Mha protected

Area within strict PAs 12.4
Area within non-strict PAs 41.7

Unit: Mha protected

Area within strict PAs 3.0
Area within non-strict PAs 10.1

Unit: Mha protected

Area within strict PAs 1.1
Area within non-strict PAs 1.6

Unit: Mha protected

Area within strict PAs 6.1
Area within non-strict PAs 28.9

Unit: Mha protected

Area within strict PAs 22.6
Area within non-strict PAs 82.3
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Adoption Trend

We calculated the annual rate of new peatland protection based on the year of PA establishment for areas established in 2000–2020. The median annual increase in peatland protection was 0.86 Mha (mean 2.0 Mha; Table 4a–d). This represents a roughly 0.8%/yr increase in peatlands within PAs, or protection of an additional 0.2%/yr of total global peatlands. This suggests that peatland protection is likely occurring at a somewhat slower rate than peatland degradation – which is estimated to be around 0.5% annually at the global scale – though this estimate is highly uncertain and spatially variable (Davidson et al., 2014).

There were large year-to-year differences in how much new peatland area was protected over this period, ranging from only 0.2 Mha in 2016 to 7.9 Mha in 2007. The rate at which peatland protection is increasing has been decreasing, with a median increase of 1.7 Mha/yr between 2000 and 2010 declining to 0.7 Mha/yr during 2010–2020. Recent median adoption of peatland protection by area is highest in boreal (0.5 Mha/yr, Table 4a) and tropical regions (0.2 Mha/yr, Table 4d), followed by temperate regions (0.1 Mha/yr, Table 4b) and subtropical regions (0.01 Mha/yr, Table 4c) (2010–2020). Scaled by total peatland area, however, recent rates of peatland protection are lowest in the subtropics (0.04%/yr), followed by the boreal (0.14%/yr) the tropics (0.16%/yr), and temperate regions (0.19%/yr).

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Table 4. Adoption trend for peatland protection in PAs of any IUCN class (2000–2020). The 25th and 75th percentiles reflect only interannual variance.

Unit: Mha of peatland protected/yr

25th percentile 0.24
mean 0.87
median (50th percentile) 0.50
75th percentile 0.89

Unit: Mha of peatland protected/yr

25th percentile 0.07
mean 0.23
median (50th percentile) 0.10
75th percentile 0.28

Unit: Mha of peatland protected/yr

25th percentile 0.00
mean 0.04
median (50th percentile) 0.01
75th percentile 0.04

Unit: Mha of peatland protected/yr

25th percentile 0.48
mean 0.84
median (50th percentile) 0.25
75th percentile 0.83
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Adoption Ceiling

We considered the adoption ceiling to include all undrained, non-coastal peatlands and estimated this to be 425 Mha, based on the Global Peatlands Database and Global Peatlands Map (UNEP, 2022; Table 5e; Appendix). We estimated that 284 Mha of undrained peatlands remain in boreal regions (Table 5a, 26 Mha in temperate regions (Table 5b, 12 Mha in the subtropics (Table 5c), and 103 Mha in the tropics (Table 5d). The adoption ceiling represents the technical upper limit to adoption of this solution.

There is substantial uncertainty in the global extent of peatlands, which is not quantified in these adoption ceiling values. Estimates of global peatland extent from recent literature include 404 Mha (Melton et al., 2022), 423 Mha (Xu et al., 2018b), 437 Mha (Müller & Joos, 2021), 463 Mha (Leifield & Menichetti, 2018), and 488 Mha (UNEP, 2022). Several studies suggest that the global peatland area may still be underestimated (Minasny et al., 2024; UNEP, 2022). 

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Table 5. Adoption ceiling: upper limit for adoption of legal protection of peatlands by biome. Values may not sum to global totals due to rounding.

Unit: Mha protected

Peatland area (Mha) 284

Unit: Mha protected

Peatland area (Mha) 26

Unit: Mha protected

Peatland area (Mha) 12

Unit: Mha protected

Peatland area (Mha) 103

Unit: Mha protected

Peatland area (Mha) 425
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Achievable Adoption

UNEP (2022) places a high priority on protecting a large majority of remaining peatlands for both climate and conservation objectives. We defined the achievable range for peatland protection as 70% (low achievable) to 90% (high achievable) of remaining undrained peatlands. Only ~19% of peatlands are currently under formal protection within PAs (UNEP, 2022; UNEP-WCMC and IUCN, 2024). However, approximately 60% of undrained peatlands are under some form of protection if peatlands within Indigenous peoples’ lands are considered (Garnett et al., 2018; UNEP, 2022; UNEP-WCMC and IUCN, 2024). While ambitious, this provides support for our selected achievable range of 70–90% (Table 6a-e). 

Ensuring effective and durable protection of these peatlands from drainage and degradation, including secure land tenure for Indigenous peoples who steward peatlands and other critical ecosystems, is a critical first step. Research suggests that local community leadership, equitable stakeholder engagement, and cross-scalar governance are needed to achieve conservation goals while also balancing social and economic outcomes through sustainable use (Atkinson & Alibašić, 2023; Cadillo & Bennett, 2024; Girkin et al., 2023; Harrison et al., 2019; Suwarno et al., 2015). Sustainable uses of peatlands include some forms of paludiculture, which can involve peatland plant cultivation, fishing, or gathering without disturbance of the hydrology or peat layer (Tan et al., 2021).

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Table 6. Range of achievable adoption of peatland protection by biome.

Unit: Mha protected

Current Adoption 54
Achievable – Low 199
Achievable – High 255
Adoption Ceiling 284

Unit: Mha protected

Current Adoption 13
Achievable – Low 18
Achievable – High 24
Adoption Ceiling 26

Unit: Mha protected

Current Adoption 3
Achievable – Low 9
Achievable – High 11
Adoption Ceiling 12

Unit: Mha protected

Current Adoption 35
Achievable – Low 72
Achievable – High 92
Adoption Ceiling 103

Unit: Mha protected

Current Adoption 105
Achievable – Low 297
Achievable – High 382
Adoption Ceiling 425
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CO₂‑eq/yr (Table 7a-e). Achievable levels of peatland protection have the potential to reduce emissions 1.3–1.7 Gt CO₂‑eq/yr, with a technical upper bound of 1.9 Gt CO₂‑eq/yr. The estimate of climate impacts under current adoption does not include the large areas of peatlands protected by Indigenous peoples but not legally recognized as PAs. Inclusion of these areas would increase the current estimated impact of peatland protection to 0.9 Gt CO₂‑eq/yr.

Other published estimates of additional emissions reductions through peatland protection are somewhat lower, with confidence intervals of 0–1.2 Gt CO₂‑eq/yr (Griscom et al., 2017; Humpenöder et al., 2020; Loisel et al., 2021; Strack et al., 2022). These studies vary in their underlying methodology and data, including the extent of peatland, the baseline rate of peatland loss, the potential for protected area expansion, which GHGs are considered, the time frame over which emissions are calculated, and whether they account for vegetation carbon loss or just emissions from the peat itself. 

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Table 7. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq , 100-yr basis/yr

Current Adoption 0.05
Achievable – Low 0.18
Achievable – High 0.24
Adoption Ceiling 0.26

Unit: Gt CO₂‑eq , 100-yr basis/yr

Current Adoption 0.06
Achievable – Low 0.08
Achievable – High 0.11
Adoption Ceiling 0.12

Unit: Gt CO₂‑eq , 100-yr basis/yr

Current Adoption 0.04
Achievable – Low 0.12
Achievable – High 0.15
Adoption Ceiling 0.17

Unit: Gt CO₂‑eq , 100-yr basis/yr

Current Adoption 0.46
Achievable – Low 0.95
Achievable – High 1.22
Adoption Ceiling 1.36

Unit: Gt CO₂‑eq , 100-yr basis/yr

Current Adoption 0.61
Achievable – Low 1.33
Achievable – High 1.71
Adoption Ceiling 1.90
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Additional Benefits

Climate Adaptation

Peatland protection can help communities adapt to extreme weather. Because peatlands regulate water flows, they can reduce the risk of droughts and floods (IUCN, 2021; Ritson et al., 2016). Evidence suggests that peatlands can provide a cooling effect to the immediate environment, lowering daytime temperatures and reducing temperature extremes between day and night (Dietrich & Behrendt, 2022; Helbig et al., 2020; Worrall et al., 2022).

Health

When peatlands are drained they are susceptible to fire. Peatland fires can significantly contribute to air pollution because of the way these fires smolder (Uda et al., 2019). Smoke and pollutants, particularly PM2.5, from peatland fires can harm respiratory health and lead to premature mortality (Marlier et al., 2019). A study of peatland fires in Indonesia estimated they contribute to the premature mortality of about 33,100 adults and about 2,900 infants annually (Hein et al., 2022). Researchers have linked exposure to PM2.5 from peatland fires to increased hospitalizations, asthma, and lost workdays (Hein et al., 2022). Peatland protection mitigates exposure to air pollution and can save money from reduced health-care expenditures (Kiely et al., 2021).

Income and Work

Peatlands support the livelihoods of nearby communities, especially those in low- and middle-income countries. In the peatlands of the Amazon and Congo basins, fishing livelihoods depend on aquatic wildlife (Thornton et al., 2020). Peatlands in the Peruvian Amazon provide important goods for trade, such as palm fruit and timber, and are used for hunting by nearby populations (Schulz et al., 2019). Peatlands can also support the livelihoods of women and contribute to gender equality. For example, raw materials – purun – from Indonesian peatlands are used by women to create and sell mats used in significant events such as births, weddings, and burials (Goib et al., 2018).

Nature Protection

Peatlands are home to a wide range of species, supporting biodiversity of flora and an abundance of wildlife (UNEP, 2022; Minayeva et al., 2017; Posa et al., 2011). Because of their unique ecosystem, peatlands provide a habitat for many rare and threatened species (Posa et al., 2011). A study of Indonesian peat swamps found that the IUCN Red List classified approximately 45% of mammals and 33% of birds living in these ecosystems as threatened, vulnerable, or endangered (Posa et al., 2011). Peatlands also support a variety of insect species (Spitzer & Danks, 2006). Because of their sensitivity to environmental changes, some peatland insects can act as indicators of peatland health and play a role in conservation efforts (Spitzer & Danks, 2006).

Water Resources

Peatlands can filter water pollutants and improve water quality and are important sources of potable water for some populations (Minayeva et al., 2017). Xu et al. (2018a) estimated that peatlands store about 10% of freshwater globally, not including glacial water. Peatlands are a significant drinking water source for people in the United Kingdom and Ireland, where they provide potable water for about 71.4 million people (Xu et al., 2018a).

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Risks

Leakage occurs when peatland drainage and clearing moves outside of protected area boundaries and is a risk of relying on peatland protection as an emissions reduction strategy (Harrison & Paoli, 2012; Strack et al., 2022). If the relocated clearing also occurs on peat soils, emissions from peatland drainage and degradation are relocated but not actually reduced. If disturbance is relocated to mineral soils, however, the disturbance-related emissions will typically be lower. Combining peatland protection with policies to reduce incentives for peatland clearing can help avoid leakage.

Peatland protection must be driven by or conducted in close collaboration with local communities, which often depend on peatlands for their livelihoods and economic advancement (Jalilov et al., 2025; Li et al., 2024a; Suwarno et al., 2016). Failure to include local communities in conservation efforts violates community sovereignty and can exacerbate existing socioeconomic inequities (Felipe Cadillo & Bennet, 2024; Thorburn & Kull, 2015). Effective peatland protection requires development of alternative income opportunities for communities currently dependent on peatland drainage, such as tourism; sustainable peatland use practices like paludiculture; or compensation for ecosystem service provisioning, including carbon storage (Evers et al., 2017; Girkin et al., 2023; Suwarno et al., 2016; Syahza et al., 2020; Tan et al., 2021; Uda et al., 2017).

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Interactions with Other Solutions

Reinforcing

Protected areas often include multiple ecosystems. Peatland protection will likely lead to protection of other ecosystems within the same areas, and the health of nearby ecosystems is improved by the services provided by intact peatlands. 

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Restored peatlands need protection to reduce the risk of future disturbance, and the health of protected peatlands can be improved through restoration of adjacent degraded peatlands.

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Reducing food loss and waste and improving diets reduce demand for agricultural land. These solutions reduce pressure to convert peatlands to agriculture use, easing expansion of protected areas.

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Competing

None

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Dashboard

Solution Basics

1 ha

t CO₂-eq (100-yr)/unit/yr
0.92
units
Current 5.4×10⁷ 01.99×10⁸2.55×10⁸
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.05 0.180.24
US$ per t CO₂-eq
0
Emergency Brake

CO₂ , CH₄, N₂O

Solution Basics

1 ha

t CO₂-eq (100-yr)/unit/yr
4.42
units
Current 1.3×10⁷ 01.8×10⁷2.4×10⁷
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.06 0.080.11
US$ per t CO₂-eq
0
Emergency Brake

CO₂ , CH₄, N₂O

Solution Basics

1 ha

t CO₂-eq (100-yr)/unit/yr
13.47
units
Current 3×10⁶ 09×10⁶1.1×10⁷
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.04 0.120.15
US$ per t CO₂-eq
0
Emergency Brake

CO₂ , CH₄, N₂O

Solution Basics

1 ha

t CO₂-eq (100-yr)/unit/yr
13.23
units
Current 3.5×10⁷ 07.2×10⁷9.2×10⁷
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.46 0.951.22
US$ per t CO₂-eq
0
Emergency Brake

CO₂ , CH₄, N₂O

Trade-offs

None

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Action Word
Protect
Solution Title
Peatlands
Classification
Highly Recommended
Lawmakers and Policymakers
  • Set clear designations of remaining peatlands and implement robust monitoring and enforcement methods.
  • Place bans or regulations on draining intact peatlands, compensate farmers for income losses, and offer extension services that promote protection and paludiculture (growing food on peatlands).
  • Grant Indigenous communities full property rights and autonomy and support them in monitoring, managing, and enforcing protected areas.
  • Incorporate peatland protection into national climate plans and international commitments.
  • Coordinate peatland protection efforts horizontally (e.g., across agencies) and vertically (e.g., across subnational, national, and international efforts), ensuring an inclusive process for local and Indigenous communities.
  • Use financial incentives such as subsidies, tax breaks, and payments for ecosystem services (PES) to protect peatlands from development.
  • Synthesize water management regulations to ensure local authorities, renters, and landowners coordinate sufficient water levels in peatlands.
  • Remove harmful agricultural, logging, and mining subsidies.
  • Map and utilize real-time data to monitor the status and condition of peatland areas.
  • Invest public funds in peatland conservation, restoration, sustainable management practices, specialized research facilities, and other R&D efforts.
  • Invest in fire warning, prevention, and response efforts and establish local volunteer fire prevention groups.
  • Work with farmers, civil society, and businesses to develop high-integrity carbon markets for peatlands.

Further information:

Practitioners
  • Refrain from draining or developing intact peatlands.
  • Invest in peatland conservation, restoration, sustainable management practices, specialized research facilities, and other R&D efforts.
  • Participate in stakeholder engagements and assist policymakers in designating peatlands, creating regulations, and implementing robust monitoring and enforcement methods.
  • Grant Indigenous communities full property rights and autonomy and support them in monitoring, managing, and enforcing protected areas.
  • Ensure protected peatlands don’t displace, violate rights, or reduce access to vital resources for local and Indigenous communities.
  • Assist in managing and monitoring protected peatlands, utilizing real-time monitoring and satellite data.
  • Create sustainable use regulations for protected peatland areas that provide resources to the local community.
  • Conduct proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Create legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over protected peatlands.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Take advantage of existing financial incentives such as subsidies, tax breaks, and payments for ecosystem services (PES) to protect peatlands from development.
  • Offer or create market mechanisms such as biodiversity offsets, payments for ecosystem services, voluntary high-integrity carbon markets, and debt-for-nature swaps to fund peatland protection.
  • Synthesize water management regulations to ensure local authorities, renters, and landowners coordinate sufficient water levels in peatlands.
  • Establish coordinating bodies for farmers, landowners, policymakers, and other stakeholders to manage protected areas holistically.
  • Invest in fire warning, prevention, and response efforts and establish local volunteer fire prevention groups.

Further information:

Business Leaders
  • Create peat-free supply chains, utilizing data, information, and the latest technology to inform product sourcing.
  • Integrate peat-free business and investment policies and practices in net zero strategies.
  • Only purchase carbon credits from high-integrity, verifiable carbon markets and do not use them as replacements for decarbonizing operations.
  • Develop financial instruments to invest in peatlands focusing on supporting Indigenous communities.
  • Conduct proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for legal protection and public relations.
  • Leverage political influence to advocate for stronger peatland protection policies at national and international levels. 

Further information:

Nonprofit Leaders
  • Ensure operations utilize peat-free products and supply chains.
  • Advocate for protecting peatlands and for public investments.
  • Assist in managing and monitoring protected peatlands, utilizing real-time monitoring and satellite data.
  • Provide financial support for protecting peatlands management, monitoring, and enforcement.
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Advocate for creating legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over protected peatlands.
  • Support high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Share data, information, and investment frameworks that successfully avoid deforestation to support protected peatlands, businesses, and investors.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for legal protection and public relations.

Further information:

Investors
  • Create peat-free investment portfolios, utilizing data, information, and the latest technology to inform investments.
  • Invest in peatland protection, monitoring, management, and enforcement mechanisms.
  • Utilize financial mechanisms such biodiversity offsets, payments for ecosystem services, voluntary high-integrity carbon markets, and debt-for-nature swaps to fund peatland protection.
  • Invest in and support Indigenous and local communities' capacity for legal protection and public relations.
  • Share data, information, and investment frameworks that successfully avoid investments that drive peatland destruction to support peatlands, other investors, and NGOs.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.

Further information:

Philanthropists and International Aid Agencies
  • Ensure operations utilize peat-free products and supply chains.
  • Advocate for protecting peatlands and for public investments.
  • Provide technical assistance to low- and middle-income countries and communities to protect peatlands.
  • Provide financial assistance to low- and middle-income countries and communities for peatland protection.
  • Assist in managing and monitoring protected peatlands, utilizing real-time monitoring and satellite data.
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Support and finance high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Advocate for creating legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over protected peatlands.
  • Support peatlands, other investors, and NGOs by sharing data, information, and investment frameworks that successfully avoid financing peatland destruction.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for legal protection and public relations.
  • Financially support Indigenous land tenure.

Further information:

Thought Leaders
  • Advocate for protecting peatlands and for public investments.
  • Assist in managing and monitoring protected peatlands, utilizing real-time monitoring and satellite data.
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Provide technical assistance to low- and middle-income countries and communities to protect peatlands.
  • Advocate for creating legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over protected peatlands.
  • Support high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Share data, information, and investment frameworks that successfully avoid deforestation to support protected peatlands, businesses, and investors.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Support Indigenous and local communities' capacity for legal protection and public relations.

Further information:

Technologists and Researchers
  • Improve mapping of peatland area, carbon content, emissions data, and monitoring methods, utilizing field measurements, models, satellite imagery, and GIS tools.
  • Develop land-use planning tools that help avoid infrastructure or development projects that may interfere with protecting peatlands or incentivize drainage.
  • Create tools for local communities to monitor peatlands, such as mobile apps, e-learning platforms, and mapping tools.
  • Develop verifiable carbon credits using technology such as blockchain to improve the integrity of carbon markets.
  • Develop supply chain tracking software for investors and businesses seeking to create peat-free portfolios and products.

Further information:

Communities, Households, and Individuals
  • Ensure purchases and investments utilize peat-free products and supply chains.
  • Advocate for protecting peatlands and for public investments.
  • Invest in fire warning, prevention, and response efforts and establish local volunteer fire prevention groups.
  • Establish coordinating bodies for farmers, landowners, policymakers, and other stakeholders to manage protected areas holistically.
  • Assist in managing and monitoring protected peatlands, utilizing real-time monitoring and satellite data.
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with protected peatlands or incentivize drainage.
  • Advocate for creating legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over protected peatlands.
  • Help shift public narratives to mobilize public action and build political will for protecting peatlands by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Support Indigenous and local communities' capacity for legal protections and public relations.

Further information:

Sources
Evidence Base

Avoided emissions from protecting peatlands: High

There is high scientific consensus that protecting peatland carbon stocks is a critical component of mitigating climate change (Girkin & Davidson, 2024; Harris et al., 2022; Leifield et al., 2019; Noon et al., 2022; Strack et al., 2022). Globally, an estimated 11–12% of peatlands have been drained for uses such as agriculture, forestry, and harvesting of peat for horticulture and fuel, with much more extensive degradation in temperate and tropical regions (~45%) than in boreal regions (~4%) (Fluet-Chouinard et al., 2023; Leifield & Menichetti, 2018; UNEP, 2022). Rates of peatland degradation are highly uncertain, and the effectiveness of PAs at reducing drainage remains unquantified. In lieu of peatland-specific data on the effectiveness of PAs at reducing drainage, we used estimates from Wolf et al. (2021), who found that PAs reduce forest loss by approximately 40.5% at the global average. 

Carbon stored in peatlands has been characterized as “irrecoverable carbon” because it takes centuries to millennia to accumulate and could not be rapidly recovered if lost (Goldstein et al., 2020; Noon et al., 2021). Degraded peatlands currently emit an estimated 1.3–1.9 Gt CO₂‑eq/yr  (excluding fires), equal to ~2–4% of total global emissions (Leifield and Menichetti., 2018; UNEP, 2022). Leifield et al. (2019) projected that without protection or restoration measures, emissions from drained peatlands could produce enough emissions to consume 10–41% of the remaining emissions budget for keeping warming below 1.5–2.0 °C. Peatland drainage had produced a cumulative 80 Gt CO₂‑eq by 2015, equal to nearly two years worth of total global emissions. In a modeling study, Humpenöder et al. (2020) projected that an additional 10.3 Mha of peatlands would be degraded by 2100 in the absence of new protection efforts, increasing annual emissions from degraded peatlands by ~25% (an additional 0.42 Gt CO₂‑eq/yr  in their study). 

The results presented in this document synthesize findings from 11 global datasets, supplemented by four regional studies on peatland loss rates in Southeast Asia. We recognize that geographic bias in the information underlying global data products creates bias, and hope this work inspires research and data sharing on this topic in underrepresented regions.

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Appendix

This analysis quantifies the emissions associated with peatland degradation and their potential reduction via establishment of Protected Areas (PAs). We leveraged multiple data products, including national-scale peatland area estimates, a peatland distribution map, shapefiles of PAs and Indigenous people’s lands, available data on rates of peatland degradation by driver, country-scale data on reductions in ecosystem degradation inside of PAs, maps of biomass carbon stocks, and biome-level emissions factors from disturbed peat soils. This appendix describes the source data products and how they were integrated. 

Peatland Extent

The global extent and distribution of peatlands is highly uncertain, and all existing peatland maps have limitations. Importantly, there is no globally accepted definition of a peatland, and different countries and data products use variable thresholds for peat depth and carbon content to define peatlands. The Global Peatland Assessment was a recent comprehensive effort to compile and harmonize existing global peatland area estimates (UNEP, 2022). We rely heavily on two products resulting from this effort: a national-scale dataset of peatland area titled the Global Peatland Database (GPD) and a map of likely peatland areas titled the Global Peatlands Map (GPM; 1 km resolution). 

Scaling Procedures

The GPM represents a known overestimate of the global peatland area, so we scaled area estimates derived from spatially explicit analyses dependent on the GPM to match total areas from the GPD. To develop a map of country-level scaling factors, we first calculated the peatland area within each country from the GPM. We calculated the country-level scaling factors as the country-level GPD values divided by the associated GPM values and converted them to a global raster. Some countries had peatland areas represented in either the GPD or GPM, but not both. Four countries had peatland areas in the GPM that were not present in the GPD, which contained 0.51 Mha of peatlands per the GPM. These areas were left unscaled. There were 38 countries with peatland areas in the GPD that did not have areas in the GPM, containing a total 0.70 Mha of peatlands. These areas, which represented 0.14% of the total peatland area in the GPD, were excluded from the scaled maps. We then multiplied the pixel-level GPM values by the scalar raster. Because of the missing countries, this scaling step very slightly overestimated (by 0.4%) total peatlands relative to the GPD. To account for this, we multiplied this intermediate map by a final global scalar (calculated as the global GPM total divided by the GPD total). This process produced a map with the same peatland distribution as the GPM but a total area that summed to that reported in the GPD.

Exclusion of Coastal Peatlands

Many coastal wetlands have peat soils, though the extent of this overlap has not been well quantified. Coastal wetlands are handled in the Protect Coastal Wetlands solution, so we excluded them from this solution to avoid double-counting. Because of the large uncertainties in both the peatland maps and available maps of coastal wetlands, we were not confident that the overlap between the two sets of maps provided a reliable estimate of the proportion of coastal wetlands located on peat soils. Therefore, we took the conservative approach of excluding all peatland pixels that were touching or overlapping with the coastline. This reduced the total peatland area considered in this solution by 5.33 Mha (1.1%). We additionally excluded degraded peatlands from the adoption ceiling and achievable range using country-level data from the GPD. Degraded peatlands will continue to be emissions sources until they are restored, so protection alone will not confer an emissions benefit.

Total Peatland Area

We conducted the analyses by latitude bands (tropical: –23.4° to 23.4°; subtropical: –35° to –23.4° and 23.4° to 35°; temperate: –35° to –50° and 35° to 50°; boreal: <–50° and >50°) in order to retain some spatial variability in emissions factors and degradation rates and drivers. We calculated the total peatland area within each latitude band based on both the scaled and unscaled peatland maps with coastal pixels excluded. We used these values as the adoption ceiling and for subsequent calculations of protected areas. 

Protected Peatland Areas

We identified protected peatland areas using the World Database on Protected Areas (WDPA, 2024), which contains boundaries for each PA and additional information, including their establishment year and IUCN management category (Ia to VI, not applicable, not reported, and not assigned). For each PA polygon, we extracted the peatland area from the unscaled version of the GPM with coastal pixels removed. 

Each PA was classified into climate zones (described above) based on the midpoint between its minimum and maximum latitude. Then, protected peatland areas were summed to the IUCN class-climate zone level, and the proportion of peatlands protected within each was calculated by dividing the protected area by the unscaled total area in each climate zone. The proportion of area protected was then multiplied by the scaled total area for each zone to calculate adoption in hectares within each IUCN class and climate zone. To evaluate trends in adoption over time, we aggregated protected areas by establishment year as reported in the WDPA. We used the same procedure to calculate the proportion of area protected using the unscaled maps, and then scale for the total area by biome. 

We used the maps of Indigenous people’s lands from Garnett et al. 2018 to identify Indigenous people’s lands that were not inside of established PAs. The total peatland area within Indigenous people’s lands process as above.

Peatland Degradation and Emissions

Broadly, we estimated annual, per-ha emissions savings from peatland protection as the difference between net carbon exchange in a protected peatland versus an unprotected peatland, accounting for all emissions pathways, the drivers of disturbance, the baseline rates of peatland disturbance, and the effectiveness of PAs at reducing ecosystem degradation. In brief, our calculation of the effectiveness of peatland protection followed Equation S1, in which the annual peatland loss avoided due to protection (%/yr) is multiplied by the 30-yr cumulative sum of emissions per ha of degraded peatland (CO₂‑eq /ha over a 30-yr period). These two terms are described in depth in the subsequent sections.

Equation S1. Effectiveness= Peatland lossavoided t=130(Emissions)  

Peatland Degradation Rates 

We calculated the avoided rate of peatland loss (%/yr) as the difference between the baseline rate of peatland loss without protection and the estimated rate of peatland loss within PAs (Equation S2), since PAs do not confer complete protection from ecosystem degradation. 

Equation S2. Peatland lossavoided =Peatland lossbaseline ✕ Reduction in loss  

We compiled baseline estimates of the current rates of peatland degradation from all causes (%/yr) from the existing literature (Table S1). Unfortunately, data on the rate of peatland loss within PAs are not available. However, satellite data have enabled in-depth, global-scale studies of the effectiveness of PAs at reducing tree cover loss. While not all peatlands are forested and degradation dynamics on peatlands can differ from those on forests writ large, these estimates are a reasonable approximation of the effectiveness of PAs at reducing peatland loss. We used the country-level estimates of the proportionate reduction in loss inside versus outside of PAs from Wolf et al. (2021), which we aggregated to latitude bands based on the median latitude of each country (Table S1).

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Table S1. Biome-level annual baseline rate of peatland loss, the effectiveness of protection at reducing loss, and the annual avoided rate of peatland loss under protection.

Climate Zone Mean Annual Peatland Loss (%/yr) Proportionate Reduction in Loss Under Protection Avoided Loss Under Protection (%/yr)
Boreal 0.3% 0.44 0.13%
Subtropic 1.2% 0.60 0.73%
Temperate 0.6% 0.56 0.33%
Tropic 1.5% 0.41 0.63%
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Emissions Factors for Peatland Degradation

Equation S3 provides an overview of the calculation of emissions from degraded peatlands. In brief, we calculated cumulative emissions as the biomass carbon stock plus the 30-yr total of CO₂‑equivalent fluxes from peat oxidation (Pox), dissolved organic carbon losses (DOC), methane from drainage ditches (Mditch), on-field methane (Mfield), on-field nitrous oxide (N) and the lost net sequestration from an intact peatland, accounting for carbon sequestration in peat and methane emissions from intact peatlands (Seqloss).

Equation S3. t=130(Emissions)=Biomass+t=130(Pox+DOC+Mditch+Mfield+N+Seqloss)  

The IPCC Tier 1 emissions factors for peatland degradation are disaggregated by climate zone (tropical, temperate, and boreal), soil fertility status (nutrient-poor versus nutrient rich), and the driver of degradation (many subclasses of forestry, cropland, grassland, and peat extraction) (IPCC 2014; Tables 2.1–2.5). Table III.5 of Annex III of the Global Peatlands Assessment provides a summarized set of emissions factors based directly on the IPCC values but aggregated to the four coarser classes of degradation drivers listed above (UNEP, 2022), which we use for our analysis. They include the following pathways: CO₂ from peat oxidation, off-site emissions from lateral transport of dissolved organic carbon (DOC), methane emissions from the field and drainage ditches, and nitrous oxide emissions from the field. Particulate organic carbon (POC) losses may be substantial, but were not included in the IPCC methodology due to uncertainties about the fate of transported POC. These emissions factors are reported as annual rates per disturbed hectare, and emissions from these pathways continue over long periods of time.

Three additional pathways that are not included in the IPCC protocol are relevant to the emissions accounting for this analysis: the loss of carbon sequestration potential from leaving the peatland intact, the methane emissions that occur from intact peatlands, and the emissions from removal of the vegetation overlying peat soils. Leifield et al. (2019) reported the annual net carbon uptake per hectare of intact peatlands, including sequestration of carbon in peat minus naturally occurring methane emissions due to the anoxic conditions. If the peatland is not disturbed, these methane emissions and carbon sequestration will persist indefinitely on an annual basis. 

We accounted for emissions from removal of biomass using a separate protocol than emissions occurring from the peat soil due to differences in the temporal dynamics of loss. While all other emissions from peat occur on an annual basis and continue for many decades or longer, emissions from biomass occur relatively quickly. Biomass clearing produces a rapid pulse of emissions from labile carbon pools followed by a declining, but persistent, rate of emissions as more recalcitrant carbon pools decay over subsequent years. The entire biomass carbon stock is likely to be lost within 30 years. Average biomass carbon stocks over the extent of the peatland distribution in the GPM were calculated by latitude band based on the above and below ground biomass carbon stock data from Spawn et al. (2020). We presumed 100% of the biomass carbon stock is lost from peatland degradation, though in many cases some amount of biomass remains following degradation, depending on the terminal land use.

Peatland Degradation Drivers 

Emissions from peatland loss depend on the driver of degradation (e.g., forestry, cropland, peat extraction; IPCC 2014). The GPD contains national-scale estimates of historical peatland loss by driver, which we used to calculate weights for each driver, reflecting the proportion of peatland loss attributable to each driver by latitude band. We took the weighted average of the driver-specific peatland emissions factors, calculated as the sum of the products of the weights and the driver-specific emissions factors.

Appendix References

Garnett, S. T., Burgess, N. D., Fa, J. E., Fernández-Llamazares, Á., Molnár, Z., Robinson, C. J., Watson, J. E. M., Zander, K. K., Austin, B., Brondizio, E. S., Collier, N. F., Duncan, T., Ellis, E., Geyle, H., Jackson, M. V., Jonas, H., Malmer, P., McGowan, B., Sivongxay, A., & Leiper, I. (2018). A spatial overview of the global importance of Indigenous lands for conservation. Nature Sustainability, 1(7), 369–374. https://doi.org/10.1038/s41893-018-0100-6

IPCC 2014, 2013 Supplement to the 2006 IPCC Guidelines for National Greenhouse Gas Inventories: Wetlands, Hiraishi, T., Krug, T., Tanabe, K., Srivastava, N., Baasansuren, J., Fukuda, M. and Troxler, T.G. (eds). Published: IPCC, Switzerland.

Leifeld, J., Wüst-Galley, C., & Page, S. (2019). Intact and managed peatland soils as a source and sink of GHGs from 1850 to 2100. Nature Climate Change, 9(12), 945–947. https://doi.org/10.1038/s41558-019-0615-5

Spawn, S. A., Sullivan, C. C., Lark, T. J., & Gibbs, H. K. (2020). Harmonized global maps of above and belowground biomass carbon density in the year 2010. Scientific Data, 7(1), 112. https://doi.org/10.1038/s41597-020-0444-4

UNEP (2022). Global Peatlands Assessment – The State of the World’s Peatlands: Evidence for action toward the conservation, restoration, and sustainable management of peatlands. Main Report. Global Peatlands Initiative. United Nations Environment Programme, Nairobi.

UNEP-WCMC and IUCN (2024), Protected Planet: The World Database on Protected Areas (WDPA) and World Database on Other Effective Area-based Conservation Measures (WD-OECM) [Online], Accessed November 2024, Cambridge, UK: UNEP-WCMC and IUCN. Available at: www.protectedplanet.net.

Wolf, C., Levi, T., Ripple, W. J., Zárrate-Charry, D. A., & Betts, M. G. (2021). A forest loss report card for the world’s protected areas. Nature Ecology & Evolution, 5(4), 520–529. https://doi.org/10.1038/s41559-021-01389-0

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Protect Forests

Submitted by Drawdown Admin on
Sector
FALO & Nature-Based Carbon Removal
Mode
Cut Emissions Remove Carbon
Cluster
Protect & Manage Ecosystems
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Fog sitting among trees of a dense forest canopy
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Summary

We define the Protect Forests solution as the long-term protection of tree-dominated ecosystems through establishment of protected areas (PAs), managed with the primary goal of conserving nature, and land tenure for Indigenous peoples. These protections reduce forest degradation, avoiding GHG emissions and ensuring continued carbon sequestration by healthy forests. This solution addresses protection of forests on mineral soils. The Protect Peatlands and Protect Coastal Wetlands solutions address protection of forested peatlands and mangrove forests, respectively, and the Restore Forests solution addresses restoring degraded forests.

Extreme weather events
Food security,Health,Equality
Nature protection,Water quality
Description for Social and Search
Protect Forests is a Highly Recommended climate solution. Healthy forests take up and store carbon. Protecting Forests ensures that intact forests stay standing, avoiding GHG emissions and maintaining their ability to absorb carbon.
Overview

Forests store carbon in biomass and soils and serve as carbon sinks, taking up an estimated 12.8 Gt CO₂‑eq/yr  (including mangroves and forested peatlands; Pan et al., 2024). Carbon stored in forests is released into the atmosphere through deforestation and degradation, which refer to forest clearing or reductions in ecosystem integrity from human influence (DellaSala et al., 2025). Humans cleared an average of 0.4% (16.3 Mha) of global forest area annually from 2001–2019 (excluding wildfire but including mangroves and forested peatlands; Hansen et al., 2013). This produced a gross flux of 7.4 Gt CO₂‑eq/yr (Harris et al., 2021), equivalent to ~14% of total global GHG emissions over that period (Dhakal et al., 2022). Different forest types store varying amounts of carbon and experience different rates of clearing; in this analysis, we individually evaluate forest protection in boreal, temperate, subtropical, and tropical regions. We included woodlands in our definition of forests because they are not differentiated in the satellite-based data used in this analysis.

We consider forests to be protected if they 1) are formally designated as PAs (UNEP-WCMC and IUCN, 2024), or 2) are mapped as Indigenous peoples’ lands in the global study by Garnett et al. (2018). The International Union for Conservation of Nature defines PAs as areas managed primarily for the long-term conservation of nature and ecosystem services. They are disaggregated into six levels of protection, ranging from strict wilderness preserves to sustainable-use areas that allow for some natural resource extraction, including logging. We included all levels of protection in this analysis, primarily because not all PAs have been classified into these categories. We rely on existing maps of Indigenous peoples’ lands but emphasize that much of their extent has not been fully mapped nor recognized for its conservation benefits (Garnett et al., 2018). Innovative and equity-driven strategies for forest protection that recognize the land rights, sovereignty, and stewardship of Indigenous peoples and local communities are critical for achieving just and effective forest protection globally (Dawson et al., 2024; Fa et al., 2020; FAO, 2024; Garnett et al., 2018; Tran et al., 2020; Zafra-Calvo et al., 2017).

Indigenous peoples’ lands and PAs reduce, but do not eliminate, forest clearing relative to unprotected areas (Baragwanath et al., 2020; Blackman & Viet 2018; Li et al., 2024; McNicol et al., 2023; Sze et al. 2022; Wolf et al., 2023; Wade et al., 2020). We rely on estimates of how effective PA are currently for this analysis but highlight that improving management to further reduce land use change within PAs is a critical component of forest protection (Jones et al., 2018; Meng et al., 2023; Vijay et al., 2018; Visconti et al., 2019; Watson et al., 2014).

Market-based strategies and other policies can complement legal protections by increasing the value of intact forests and reducing incentives for clearing (e.g., Garett et al., 2019; Golub et al., 2021; Heilmayr et al., 2020; Lambin et al., 2018; Levy et al., 2023; Macdonald et al., 2024; Marin et al., 2022; Villoria et al., 2022; West et al., 2023). The estimates in this report are based on legal protection alone because the effectiveness of market-based strategies is difficult to quantify, but strategies such as sustainable commodities programs, reducing or redirecting agricultural subsidies, and strategic infrastructure planning will be further discussed in a future update. 

Adams, V. M., Iacona, G. D., & Possingham, H. P. (2019). Weighing the benefits of expanding protected areas versus managing existing ones. Nature Sustainability, 2(5), 404–411. Link to source: https://doi.org/10.1038/s41893-019-0275-5

Anderegg, W. R. L., Trugman, A. T., Badgley, G., Anderson, C. M., Bartuska, A., Ciais, P., Cullenward, D., Field, C. B., Freeman, J., Goetz, S. J., Hicke, J. A., Huntzinger, D., Jackson, R. B., Nickerson, J., Pacala, S., & Randerson, J. T. (2020). Climate-driven risks to the climate mitigation potential of forests. Science, 368(6497), eaaz7005. Link to source: https://doi.org/10.1126/science.aaz7005

Arneth, A., Leadley, P., Claudet, J., Coll, M., Rondinini, C., Rounsevell, M. D. A., Shin, Y.-J., Alexander, P., & Fuchs, R. (2023). Making protected areas effective for biodiversity, climate and food. Global Change Biology, 29(14), 3883–3894. Link to source: https://doi.org/10.1111/gcb.16664

Baragwanath, K., & Bayi, E. (2020). Collective property rights reduce deforestation in the Brazilian Amazon. Proceedings of the National Academy of Sciences, 117(34), 20495–20502. Link to source: https://doi.org/10.1073/pnas.1917874117

Barnes, M. D., Glew, L., Wyborn, C., & Craigie, I. D. (2018). Prevent perverse outcomes from global protected area policy. Nature Ecology & Evolution, 2(5), 759–762. Link to source: https://doi.org/10.1038/s41559-018-0501-y

Bliege Bird, R., & Nimmo, D. (2018). Restore the lost ecological functions of people. Nature Ecology & Evolution, 2(7), 1050–1052. Link to source: https://doi.org/10.1038/s41559-018-0576-5

Blackman, A., & Veit, P. (2018). Titled Amazon Indigenous Communities Cut Forest Carbon Emissions. Ecological Economics, 153, 56–67. Link to source: https://doi.org/10.1016/j.ecolecon.2018.06.016

Brennan, A., Naidoo, R., Greenstreet, L., Mehrabi, Z., Ramankutty, N., & Kremen, C. (2022). Functional connectivity of the world’s protected areas. Science, 376(6597), 1101–1104. Link to source: https://doi.org/10.1126/science.abl8974

Brinck, K., Fischer, R., Groeneveld, J., Lehmann, S., Dantas De Paula, M., Pütz, S., Sexton, J. O., Song, D., & Huth, A. (2017). High resolution analysis of tropical forest fragmentation and its impact on the global carbon cycle. Nature Communications, 8(1), 14855. Link to source: https://doi.org/10.1038/ncomms14855

Bruner, A. G., Gullison, R. E., & Balmford, A. (2004). Financial Costs and Shortfalls of Managing and Expanding Protected-Area Systems in Developing Countries. BioScience, 54(12), 1119–1126. Link to source: https://doi.org/10.1641/0006-3568(2004)054[1119:FCASOM]2.0.CO;2

Buotte, P. C., Law, B. E., Ripple, W. J., & Berner, L. T. (2020). Carbon sequestration and biodiversity co-benefits of preserving forests in the western United States. Ecological Applications, 30(2), e02039. Link to source: https://doi.org/10.1002/eap.2039

Curtis, P. G., Slay, C. M., Harris, N. L., Tyukavina, A., & Hansen, M. C. (2018). Classifying drivers of global forest loss. Science, 361(6407), 1108–1111. Link to source: https://doi.org/10.1126/science.aau3445

Dawson, N. M., Coolsaet, B., Bhardwaj, A., Booker, F., Brown, D., Lliso, B., Loos, J., Martin, A., Oliva, M., Pascual, U., Sherpa, P., & Worsdell, T. (2024). Is it just conservation? A typology of Indigenous peoples’ and local communities’ roles in conserving biodiversity. One Earth, 7(6), 1007–1021. Link to source: https://doi.org/10.1016/j.oneear.2024.05.001

de Souza, S. E. X. F., Vidal, E., Chagas, G. de F., Elgar, A. T., & Brancalion, P. H. S. (2016). Ecological outcomes and livelihood benefits of community-managed agroforests and second growth forests in Southeast Brazil. Biotropica, 48(6), 868–881. Link to source: https://doi.org/10.1111/btp.12388

Delacote, P., Le Velly, G., & Simonet, G. (2022). Revisiting the location bias and additionality of REDD+ projects: The role of project proponents status and certification. Resource and Energy Economics, 67, 101277. Link to source: https://doi.org/10.1016/j.reseneeco.2021.101277

Delacote, P., Velly, G. L., & Simonet, G. (2024). Distinguishing potential and effective additionality of forest conservation interventions. Environment and Development Economics, 1–21. Link to source: https://doi.org/10.1017/S1355770X24000202

DellaSala, D. A., Mackey, B., Kormos, C. F., Young, V., Boan, J. J., Skene, J. L., Lindenmayer, D. B., Kun, Z., Selva, N., Malcolm, J. R., & Laurance, W. F. (2025). Measuring forest degradation via ecological-integrity indicators at multiple spatial scales. Biological Conservation, 302, 110939. Link to source: https://doi.org/10.1016/j.biocon.2024.110939

Dhakal, S., J.C. Minx, F.L. Toth, A. Abdel-Aziz, M.J. Figueroa Meza, K. Hubacek, I.G.C. Jonckheere, Yong-Gun Kim, G.F. Nemet, S. Pachauri, X.C. Tan, T. Wiedmann, 2022: Emissions Trends and Drivers. In IPCC, 2022: Climate Change 2022: Mitigation of Climate Change. Contribution of Working Group III to the Sixth Assessment Report of the Intergovernmental Panel on Climate Change [P.R. Shukla, J. Skea, R. Slade, A. Al Khourdajie, R. van Diemen, D. McCollum, M. Pathak, S. Some, P. Vyas, R. Fradera, M. Belkacemi, A. Hasija, G. Lisboa, S. Luz, J. Malley, (eds.)]. Cambridge University Press, Cambridge, UK and New York, NY, USA. Link to source: https://doi.org/10.1017/9781009157926.004

Dinerstein, E., Joshi, A. R., Hahn, N. R., Lee, A. T. L., Vynne, C., Burkart, K., Asner, G. P., Beckham, C., Ceballos, G., Cuthbert, R., Dirzo, R., Fankem, O., Hertel, S., Li, B. V., Mellin, H., Pharand-Deschênes, F., Olson, D., Pandav, B., Peres, C. A., … Zolli, A. (2024). Conservation Imperatives: Securing the last unprotected terrestrial sites harboring irreplaceable biodiversity. Frontiers in Science, 2. Link to source: https://doi.org/10.3389/fsci.2024.1349350

Dye, A. W., Houtman, R. M., Gao, P., Anderegg, W. R. L., Fettig, C. J., Hicke, J. A., Kim, J. B., Still, C. J., Young, K., & Riley, K. L. (2024). Carbon, climate, and natural disturbance: A review of mechanisms, challenges, and tools for understanding forest carbon stability in an uncertain future. Carbon Balance and Management, 19(1), 35. Link to source: https://doi.org/10.1186/s13021-024-00282-0

Ellison, D., N. Futter, M., & Bishop, K. (2012). On the forest cover–water yield debate: From demand- to supply-side thinking. Global Change Biology, 18(3), 806–820. Link to source: https://doi.org/10.1111/j.1365-2486.2011.02589.x

ESA CCI (2019). Copernicus Climate Change Service, Climate Data Store: Land cover classification gridded maps from 1992 to present derived from satellite observation. Copernicus Climate Change Service (C3S) Climate Data Store (CDS). Accessed November 2024. doi: 10.24381/cds.006f2c9a

Fa, J. E., Watson, J. E., Leiper, I., Potapov, P., Evans, T. D., Burgess, N. D., Molnár, Z., Fernández-Llamazares, Á., Duncan, T., Wang, S., Austin, B. J., Jonas, H., Robinson, C. J., Malmer, P., Zander, K. K., Jackson, M. V., Ellis, E., Brondizio, E. S., & Garnett, S. T. (2020). Importance of Indigenous Peoples’ lands for the conservation of Intact Forest Landscapes. Frontiers in Ecology and the Environment, 18(3), 135–140. Link to source: https://doi.org/10.1002/fee.2148

FAO. 2024. The State of the World’s Forests 2024 – Forest-sector innovations towards a more sustainable future. Rome. https://doi.org/10.4060/cd1211en

Filoso, S., Bezerra, M. O., Weiss, K. C. B., & Palmer, M. A. (2017). Impacts of forest restoration on water yield: A systematic review. PLOS ONE, 12(8), e0183210. Link to source: https://doi.org/10.1371/journal.pone.0183210

Fletcher, M.-S., Hamilton, R., Dressler, W., & Palmer, L. (2021). Indigenous knowledge and the shackles of wilderness. Proceedings of the National Academy of Sciences, 118(40), e2022218118. Link to source: https://doi.org/10.1073/pnas.2022218118

Fuller, C., Ondei, S., Brook, B. W., & Buettel, J. C. (2020). Protected-area planning in the Brazilian Amazon should prioritize additionality and permanence, not leakage mitigation. Biological Conservation, 248, 108673. Link to source: https://doi.org/10.1016/j.biocon.2020.108673

Gallemore, C., Bowsher, A., Atheeque, A., Groff, E., & Furtado, J. (n.d.). The geography of avoided deforestation and sustainable forest management offsets: The enduring question of additionality. Climate Policy, 0(0), 1–17. Link to source: https://doi.org/10.1080/14693062.2024.2383418

Gallemore, C., Bowsher, A., Atheeque, A., Groff, E., & Furtado, J. (2023). The geography of avoided deforestation and sustainable forest management offsets: The enduring question of additionality. Climate Policy, 0(0), 1–17. Link to source: https://doi.org/10.1080/14693062.2024.2383418

Garnett, S. T., Burgess, N. D., Fa, J. E., Fernández-Llamazares, Á., Molnár, Z., Robinson, C. J., Watson, J. E. M., Zander, K. K., Austin, B., Brondizio, E. S., Collier, N. F., Duncan, T., Ellis, E., Geyle, H., Jackson, M. V., Jonas, H., Malmer, P., McGowan, B., Sivongxay, A., & Leiper, I. (2018). A spatial overview of the global importance of Indigenous lands for conservation. Nature Sustainability, 1(7), 369–374. Link to source: https://doi.org/10.1038/s41893-018-0100-6

Garrett, R. D., Levy, S., Carlson, K. M., Gardner, T. A., Godar, J., Clapp, J., Dauvergne, P., Heilmayr, R., le Polain de Waroux, Y., Ayre, B., Barr, R., Døvre, B., Gibbs, H. K., Hall, S., Lake, S., Milder, J. C., Rausch, L. L., Rivero, R., Rueda, X., … Villoria, N. (2019). Criteria for effective zero-deforestation commitments. Global Environmental Change, 54, 135–147. Link to source: https://doi.org/10.1016/j.gloenvcha.2018.11.003

Gibbs, H. K., Ruesch, A. S., Achard, F., Clayton, M. K., Holmgren, P., Ramankutty, N., & Foley, J. A. (2010). Tropical forests were the primary sources of new agricultural land in the 1980s and 1990s. Proceedings of the National Academy of Sciences, 107(38), 16732–16737. Link to source: https://doi.org/10.1073/pnas.0910275107

Golub, A., Herrera, D., Leslie, G., Pietracci, B., & Lubowski, R. (2021). A real options framework for reducing emissions from deforestation: Reconciling short-term incentives with long-term benefits from conservation and agricultural intensification. Ecosystem Services, 49, 101275. Link to source: https://doi.org/10.1016/j.ecoser.2021.101275

Graham, V., Geldmann, J., Adams, V. M., Negret, P. J., Sinovas, P., & Chang, H.-C. (2021). Southeast Asian protected areas are effective in conserving forest cover and forest carbon stocks compared to unprotected areas. Scientific Reports, 11(1), 23760. Link to source: https://doi.org/10.1038/s41598-021-03188-w

Grantham, H. S., Duncan, A., Evans, T. D., Jones, K. R., Beyer, H. L., Schuster, R., Walston, J., Ray, J. C., Robinson, J. G., Callow, M., Clements, T., Costa, H. M., DeGemmis, A., Elsen, P. R., Ervin, J., Franco, P., Goldman, E., Goetz, S., Hansen, A., … Watson, J. E. M. (2020). Anthropogenic modification of forests means only 40% of remaining forests have high ecosystem integrity. Nature Communications, 11(1), 5978. Link to source: https://doi.org/10.1038/s41467-020-19493-3

Gray, C. L., Hill, S. L. L., Newbold, T., Hudson, L. N., Börger, L., Contu, S., Hoskins, A. J., Ferrier, S., Purvis, A., & Scharlemann, J. P. W. (2016). Local biodiversity is higher inside than outside terrestrial protected areas worldwide. Nature Communications, 7(1), 12306. Link to source: https://doi.org/10.1038/ncomms12306

Griscom, B. W., Adams, J., Ellis, P. W., Houghton, R. A., Lomax, G., Miteva, D. A., Schlesinger, W. H., Shoch, D., Siikamäki, J. V., Smith, P., Woodbury, P., Zganjar, C., Blackman, A., Campari, J., Conant, R. T., Delgado, C., Elias, P., Gopalakrishna, T., Hamsik, M. R., … Fargione, J. (2017). Natural climate solutions. Proceedings of the National Academy of Sciences, 114(44), 11645–11650. Link to source: https://doi.org/10.1073/pnas.1710465114

Hansen, M. C., Potapov, P. V., Moore, R., Hancher, M., Turubanova, S. A., Tyukavina, A., Thau, D., Stehman, S. V., Goetz, S. J., Loveland, T. R., Kommareddy, A., Egorov, A., Chini, L., Justice, C. O., & Townshend, J. R. G. (2013). High-Resolution Global Maps of 21st-Century Forest Cover Change. Science, 342(6160), 850–853. Link to source: https://doi.org/10.1126/science.1244693. Data available on-line from: http://earthenginepartners.appspot.com/science-2013-global-forest. Accessed through Global Forest Watch on 01/12/2024. www.globalforestwatch.org

Harris, N. L., Gibbs, D. A., Baccini, A., Birdsey, R. A., de Bruin, S., Farina, M., Fatoyinbo, L., Hansen, M. C., Herold, M., Houghton, R. A., Potapov, P. V., Suarez, D. R., Roman-Cuesta, R. M., Saatchi, S. S., Slay, C. M., Turubanova, S. A., & Tyukavina, A. (2021). Global maps of twenty-first century forest carbon fluxes. Nature Climate Change, 11(3), 234–240. Link to source: https://doi.org/10.1038/s41558-020-00976-6

Heilmayr, R., Rausch, L. L., Munger, J., & Gibbs, H. K. (2020). Brazil’s Amazon Soy Moratorium reduced deforestation. Nature Food, 1(12), 801–810. Link to source: https://doi.org/10.1038/s43016-020-00194-5

Herrera, D., Ellis, A., Fisher, B., Golden, C. D., Johnson, K., Mulligan, M., Pfaff, A., Treuer, T., & Ricketts, T. H. (2017). Upstream watershed condition predicts rural children’s health across 35 developing countries. Nature Communications, 8(1), 811. Link to source: https://doi.org/10.1038/s41467-017-00775-2

Herrera, D., Pfaff, A., & Robalino, J. (2019). Impacts of protected areas vary with the level of government: Comparing avoided deforestation across agencies in the Brazilian Amazon. Proceedings of the National Academy of Sciences, 116(30), 14916–14925. Link to source: https://doi.org/10.1073/pnas.1802877116

Jones, K. R., Venter, O., Fuller, R. A., Allan, J. R., Maxwell, S. L., Negret, P. J., & Watson, J. E. M. (2018). One-third of global protected land is under intense human pressure. Science, 360(6390), 788–791. Link to source: https://doi.org/10.1126/science.aap9565

Kolden, C. A., Abatzoglou, J. T., Jones, M. W., & Jain, P. (2024). Wildfires in 2023. Nature Reviews Earth & Environment, 5(4), 238–240. Link to source: https://doi.org/10.1038/s43017-024-00544-y

Kreye, M. M., Adams, D. C., & Escobedo, F. J. (2014). The Value of Forest Conservation for Water Quality Protection. Forests, 5(5), Article 5. Link to source: https://doi.org/10.3390/f5050862

Lambin, E. F., Gibbs, H. K., Heilmayr, R., Carlson, K. M., Fleck, L. C., Garrett, R. D., le Polain de Waroux, Y., McDermott, C. L., McLaughlin, D., Newton, P., Nolte, C., Pacheco, P., Rausch, L. L., Streck, C., Thorlakson, T., & Walker, N. F. (2018). The role of supply-chain initiatives in reducing deforestation. Nature Climate Change, 8(2), 109–116. Link to source: https://doi.org/10.1038/s41558-017-0061-1

Lawrence, D., Coe, M., Walker, W., Verchot, L., & Vandecar, K. (2022). The unseen effects of deforestation: biophysical effects on climate. Frontiers in Forests and Global Change, 5. Link to source: https://doi.org/10.3389/ffgc.2022.756115

Levy, S. A., Cammelli, F., Munger, J., Gibbs, H. K., & Garrett, R. D. (2023). Deforestation in the Brazilian Amazon could be halved by scaling up the implementation of zero-deforestation cattle commitments. Global Environmental Change, 80, 102671. Link to source: https://doi.org/10.1016/j.gloenvcha.2023.102671

Li, G., Fang, C., Watson, J. E. M., Sun, S., Qi, W., Wang, Z., & Liu, J. (2024). Mixed effectiveness of global protected areas in resisting habitat loss. Nature Communications, 15(1), 8389. Link to source: https://doi.org/10.1038/s41467-024-52693-9

Lindenmayer, D. (2024). Key steps toward expanding protected areas to conserve global biodiversity. Frontiers in Science, 2. Link to source: https://doi.org/10.3389/fsci.2024.1426480

Lutz, J. A., Furniss, T. J., Johnson, D. J., Davies, S. J., Allen, D., Alonso, A., Anderson-Teixeira, K. J., Andrade, A., Baltzer, J., Becker, K. M. L., Blomdahl, E. M., Bourg, N. A., Bunyavejchewin, S., Burslem, D. F. R. P., Cansler, C. A., Cao, K., Cao, M., Cárdenas, D., Chang, L.-W., … Zimmerman, J. K. (2018). Global importance of large-diameter trees. Global Ecology and Biogeography, 27(7), 849–864. Link to source: https://doi.org/10.1111/geb.12747

Macdonald, K., Diprose, R., Grabs, J., Schleifer, P., Alger, J., Bahruddin, Brandao, J., Cashore, B., Chandra, A., Cisneros, P., Delgado, D., Garrett, R., & Hopkinson, W. (2024). Jurisdictional approaches to sustainable agro-commodity governance: The state of knowledge and future research directions. Earth System Governance, 22, 100227. Link to source: https://doi.org/10.1016/j.esg.2024.100227

McCallister, M., Krasovskiy, A., Platov, A., Pietracci, B., Golub, A., Lubowski, R., & Leslie, G. (2022). Forest protection and permanence of reduced emissions. Frontiers in Forests and Global Change, 5. Link to source: https://doi.org/10.3389/ffgc.2022.928518

Marin, F. R., Zanon, A. J., Monzon, J. P., Andrade, J. F., Silva, E. H. F. M., Richter, G. L., Antolin, L. A. S., Ribeiro, B. S. M. R., Ribas, G. G., Battisti, R., Heinemann, A. B., & Grassini, P. (2022). Protecting the Amazon forest and reducing global warming via agricultural intensification. Nature Sustainability, 5(12), 1018–1026. Link to source: https://doi.org/10.1038/s41893-022-00968-8

McNicol, I. M., Keane, A., Burgess, N. D., Bowers, S. J., Mitchard, E. T. A., & Ryan, C. M. (2023). Protected areas reduce deforestation and degradation and enhance woody growth across African woodlands. Communications Earth & Environment, 4(1), 1–14. Link to source: https://doi.org/10.1038/s43247-023-01053-4

Melo, F. P. L., Parry, L., Brancalion, P. H. S., Pinto, S. R. R., Freitas, J., Manhães, A. P., Meli, P., Ganade, G., & Chazdon, R. L. (2021). Adding forests to the water–energy–food nexus. Nature Sustainability, 4(2), 85–92. Link to source: https://doi.org/10.1038/s41893-020-00608-z

Meng, Z., Dong, J., Ellis, E. C., Metternicht, G., Qin, Y., Song, X.-P., Löfqvist, S., Garrett, R. D., Jia, X., & Xiao, X. (2023). Post-2020 biodiversity framework challenged by cropland expansion in protected areas. Nature Sustainability, 6(7), 758–768. Link to source: https://doi.org/10.1038/s41893-023-01093-w

Morales-Hidalgo, D., Oswalt, S. N., & Somanathan, E. (2015). Status and trends in global primary forest, protected areas, and areas designated for conservation of biodiversity from the Global Forest Resources Assessment 2015. Forest Ecology and Management, 352, 68–77. Link to source: https://doi.org/10.1016/j.foreco.2015.06.011

Mykleby, P. M., Snyder, P. K., & Twine, T. E. (2017). Quantifying the trade-off between carbon sequestration and albedo in midlatitude and high-latitude North American forests. Geophysical Research Letters, 44(5), 2493–2501. Link to source: https://doi.org/10.1002/2016GL071459

Nabuurs, G-J., R. Mrabet, A. Abu Hatab, M. Bustamante, H. Clark, P. Havlík, J. House, C. Mbow, K.N. Ninan, A. Popp, S. Roe, B. Sohngen, S. Towprayoon, 2022: Agriculture, Forestry and Other Land Uses (AFOLU). In IPCC, 2022: Climate Change 2022: Mitigation of Climate Change. Contribution of Working Group III to the Sixth Assessment Report of the Intergovernmental Panel on Climate Change [P.R. Shukla, J. Skea, R. Slade, A. Al Khourdajie, R. van Diemen, D. McCollum, M. Pathak, S. Some, P. Vyas, R. Fradera, M. Belkacemi, A. Hasija, G. Lisboa, S. Luz, J. Malley, (eds.)]. Cambridge University Press, Cambridge, UK and New York, NY, USA. Link to source: https://doi.org/10.1017/9781009157926.009

Naidoo, R., Gerkey, D., Hole, D., Pfaff, A., Ellis, A. M., Golden, C. D., Herrera, D., Johnson, K., Mulligan, M., Ricketts, T. H., & Fisher, B. (2019). Evaluating the impacts of protected areas on human well-being across the developing world. Science Advances, 5(4), eaav3006. Link to source: https://doi.org/10.1126/sciadv.aav3006

Oldekop, J. A., Rasmussen, L. V., Agrawal, A., Bebbington, A. J., Meyfroidt, P., Bengston, D. N., Blackman, A., Brooks, S., Davidson-Hunt, I., Davies, P., Dinsi, S. C., Fontana, L. B., Gumucio, T., Kumar, C., Kumar, K., Moran, D., Mwampamba, T. H., Nasi, R., Nilsson, M., … Wilson, S. J. (2020). Forest-linked livelihoods in a globalized world. Nature Plants, 6(12), 1400–1407. Link to source: https://doi.org/10.1038/s41477-020-00814-9

Pan, Y., Birdsey, R. A., Phillips, O. L., Houghton, R. A., Fang, J., Kauppi, P. E., Keith, H., Kurz, W. A., Ito, A., Lewis, S. L., Nabuurs, G.-J., Shvidenko, A., Hashimoto, S., Lerink, B., Schepaschenko, D., Castanho, A., & Murdiyarso, D. (2024). The enduring world forest carbon sink. Nature, 631(8021), 563–569. Link to source: https://doi.org/10.1038/s41586-024-07602-x

Phillips, C. A., Rogers, B. M., Elder, M., Cooperdock, S., Moubarak, M., Randerson, J. T., & Frumhoff, P. C. (2022). Escalating carbon emissions from North American boreal forest wildfires and the climate mitigation potential of fire management. Science Advances, 8(17), eabl7161. Link to source: https://doi.org/10.1126/sciadv.abl7161

Reddington, C. L., Butt, E. W., Ridley, D. A., Artaxo, P., Morgan, W. T., Coe, H., & Spracklen, D. V. (2015). Air quality and human health improvements from reductions in deforestation-related fire in Brazil. Nature Geoscience, 8(10), 768–771. Link to source: https://doi.org/10.1038/ngeo2535

Richter, J., Goldman, E., Harris, N., Gibbs, D., Rose, M., Peyer, S., Richardson, S., & Velappan, H. (2024). Spatial Database of Planted Trees (SDPT Version 2.0) [Dataset]. Link to source: https://doi.org/10.46830/writn.23.00073

Rogers, B. M., Mackey, B., Shestakova, T. A., Keith, H., Young, V., Kormos, C. F., DellaSala, D. A., Dean, J., Birdsey, R., Bush, G., Houghton, R. A., & Moomaw, W. R. (2022). Using ecosystem integrity to maximize climate mitigation and minimize risk in international forest policy. Frontiers in Forests and Global Change, 5. Link to source: https://doi.org/10.3389/ffgc.2022.929281

Ruseva, T., Marland, E., Szymanski, C., Hoyle, J., Marland, G., & Kowalczyk, T. (2017). Additionality and permanence standards in California’s Forest Offset Protocol: A review of project and program level implications. Journal of Environmental Management, 198, 277–288. Link to source: https://doi.org/10.1016/j.jenvman.2017.04.082

Sarira, T. V., Zeng, Y., Neugarten, R., Chaplin-Kramer, R., & Koh, L. P. (2022). Co-benefits of forest carbon projects in Southeast Asia. Nature Sustainability, 5(5), 393–396. Link to source: https://doi.org/10.1038/s41893-022-00849-0

Seymour, F., Wolosin, M., & Gray, E. (2022, October 23). Policies underestimate forests’ full effect on the climate. World Resources Institute. Link to source: https://www.wri.org/insights/how-forests-affect-climate

Smith, C., Baker, J. C. A., & Spracklen, D. V. (2023). Tropical deforestation causes large reductions in observed precipitation. Nature, 615(7951), 270–275. Link to source: https://doi.org/10.1038/s41586-022-05690-1

Soto-Navarro, C., Ravilious, C., Arnell, A., de Lamo, X., Harfoot, M., Hill, S. L. L., Wearn, O. R., Santoro, M., Bouvet, A., Mermoz, S., Le Toan, T., Xia, J., Liu, S., Yuan, W., Spawn, S. A., Gibbs, H. K., Ferrier, S., Harwood, T., Alkemade, R., … Kapos, V. (2020). Mapping co-benefits for carbon storage and biodiversity to inform conservation policy and action. Philosophical Transactions of the Royal Society B: Biological Sciences, 375(1794), 20190128. Link to source: https://doi.org/10.1098/rstb.2019.0128

Sunderlin, W. D., Angelsen, A., Belcher, B., Burgers, P., Nasi, R., Santoso, L., & Wunder, S. (2005). Livelihoods, forests, and conservation in developing countries: An Overview. World Development, 33(9), 1383–1402. Link to source: https://doi.org/10.1016/j.worlddev.2004.10.004

Sweeney, B. W., Bott, T. L., Jackson, J. K., Kaplan, L. A., Newbold, J. D., Standley, L. J., Hession, W. C., & Horwitz, R. J. (2004). Riparian deforestation, stream narrowing, and loss of stream ecosystem services. Proceedings of the National Academy of Sciences, 101(39), 14132–14137. Link to source: https://doi.org/10.1073/pnas.0405895101

Sze, J. S., Carrasco, L. R., Childs, D., & Edwards, D. P. (2022). Reduced deforestation and degradation in Indigenous Lands pan-tropically. Nature Sustainability, 5(2), 123–130. Link to source: https://doi.org/10.1038/s41893-021-00815-2

Tauli-Corpuz, V., Alcorn, J., Molnar, A., Healy, C., & Barrow, E. (2020). Cornered by PAs: Adopting rights-based approaches to enable cost-effective conservation and climate action. World Development, 130, 104923. Link to source: https://doi.org/10.1016/j.worlddev.2020.104923

Tran, T. C., Ban, N. C., & Bhattacharyya, J. (2020). A review of successes, challenges, and lessons from Indigenous protected and conserved areas. Biological Conservation, 241, 108271. Link to source: https://doi.org/10.1016/j.biocon.2019.108271

UNEP-WCMC and IUCN (2024), Protected Planet: The World Database on Protected Areas (WDPA) and World Database on Other Effective Area-based Conservation Measures (WD-OECM) [Online], Accessed November 2024, Cambridge, UK: UNEP-WCMC and IUCN. Available at: www.protectedplanet.net.

Vijay, V., Fisher, J. R. B., & Armsworth, P. R. (2022). Co-benefits for terrestrial biodiversity and ecosystem services available from contrasting land protection policies in the contiguous United States. Conservation Letters, 15(5), e12907. Link to source: https://doi.org/10.1111/conl.12907

Villoria, N., Garrett, R., Gollnow, F., & Carlson, K. (2022). Leakage does not fully offset soy supply-chain efforts to reduce deforestation in Brazil. Nature Communications, 13(1), 5476. Link to source: https://doi.org/10.1038/s41467-022-33213-z

Visconti, P., Butchart, S. H. M., Brooks, T. M., Langhammer, P. F., Marnewick, D., Vergara, S., Yanosky, A., & Watson, J. E. M. (2019). Protected area targets post-2020. Science, 364(6437), 239–241. Link to source: https://doi.org/10.1126/science.aav6886

Wade, C. M., Austin, K. G., Cajka, J., Lapidus, D., Everett, K. H., Galperin, D., Maynard, R., & Sobel, A. (2020). What Is Threatening Forests in Protected Areas? A Global Assessment of Deforestation in Protected Areas, 2001–2018. Forests, 11(5), Article 5. Link to source: https://doi.org/10.3390/f11050539

Waldron, A., Adams, V., Allan, J., Arnell, A., Asner, G., Atkinson, S., Baccini, A., Baillie, J., Balmford, A., & Austin Beau, J. (2020). Protecting 30% of the planet for nature: Costs, benefits and economic implications. Link to source: https://pure.iiasa.ac.at/id/eprint/16560/1/Waldron_Report_FINAL_sml.pdf

Walton, Z. L., Poudyal, N. C., Hepinstall-Cymerman, J., Johnson Gaither, C., & Boley, B. B. (2016). Exploring the role of forest resources in reducing community vulnerability to the heat effects of climate change. Forest Policy and Economics, 71, 94–102. Link to source: https://doi.org/10.1016/j.forpol.2015.09.001

Watson, J. E. M., Dudley, N., Segan, D. B., & Hockings, M. (2014). The performance and potential of protected areas. Nature, 515(7525), 67–73. Link to source: https://doi.org/10.1038/nature13947

West, T. A. P., Wunder, S., Sills, E. O., Börner, J., Rifai, S. W., Neidermeier, A. N., Frey, G. P., & Kontoleon, A. (2023). Action needed to make carbon offsets from forest conservation work for climate change mitigation. Science, 381(6660), 873–877. Link to source: https://doi.org/10.1126/science.ade3535

Wolf, C., Levi, T., Ripple, W. J., Zárrate-Charry, D. A., & Betts, M. G. (2021). A forest loss report card for the world’s protected areas. Nature Ecology & Evolution, 5(4), 520–529. Link to source: https://doi.org/10.1038/s41559-021-01389-0

Zafra-Calvo, N., Pascual, U., Brockington, D., Coolsaet, B., Cortes-Vazquez, J. A., Gross-Camp, N., Palomo, I., & Burgess, N. D. (2017). Towards an indicator system to assess equitable management in protected areas. Biological Conservation, 211, 134–141. Link to source: https://doi.org/10.1016/j.biocon.2017.05.014

Credits

Lead Fellow

  • Avery Driscoll

Contributors

  • Ruthie Burrows, Ph.D.

  • James Gerber, Ph.D.

  • Yusuf Jameel, Ph.D. 

  • Daniel Jasper

  • Alex Sweeney

Internal Reviewers

  • Hannah Henkin

  • Megan Matthews, Ph.D.

  • Ted Otte

  • Christina Swanson, Ph.D.

  • Paul C. West, Ph.D.

Effectiveness

We estimated that one ha of forest protection provides total carbon benefits of 0.299–2.204 t CO₂‑eq/yr depending on the biome (Table 1a–d; Appendix). This effectiveness estimate includes avoided emissions and preserved sequestration capacity attributable to the reduction in forest loss conferred by protection (Equation 1). First, we calculated the difference between the rate of human-caused forest loss outside of PAs (Forest lossbaseline) and the rate inside of PAs (Forest lossprotected). We then multiplied the annual rate of avoided forest loss by the sum of the carbon stored in one hectare of forest (Carbonstock) and the amount of carbon that one hectare of intact forest takes up over a 30-yr timeframe (Carbonsequestration).

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Equation 1.

$$\mathit{Effectiveness} = (\mathit{Forest\ loss}_{\mathit{baseline}} - \mathit{Forest\ loss}_{\mathit{protected}}) \times (\mathit{Carbon_{\mathit{stock}}} + \mathit{Carbon_{\mathit{sequestration}}})$$

Each of these factors varies across biomes. Based on our definition, for instance, the effectiveness of forest protection in boreal forests is lower than that in tropical and subtropical forests primarily because the former face lower rates of human-caused forest loss (though greater wildfire impacts). Importantly, the effectiveness of forest protection as defined here reflects only a small percentage of the carbon stored (394 t CO₂‑eq ) and absorbed (4.25 t CO₂‑eq/yr ) per hectare of forest (Harris et al., 2021). This is because humans clear ~0.4% of forest area annually, and forest protection is estimated to reduce human-caused forest loss by an average of 40.5% (Curtis et al., 2018; Wolf et al., 2023). 

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Table 1. Effectiveness at reducing emissions and sequestering carbon, with carbon sequestration calculated over a 30-yr timeframe. Differences in values between biomes are driven by variation in forest carbon stocks and sequestration rates, baseline rates of forest loss, and effectiveness of PAs at reducing forest loss. See the Appendix for source data and calculation details. Emissions and sequestration values may not sum to total effectiveness due to rounding.

Unit: t CO₂‑eq/ha/yr, 100-yr basis

Avoided emissions 0.207
Sequestration 0.091
Total effectiveness 0.299

Unit: t CO₂‑eq/ha/yr, 100-yr basis

Avoided emissions 0.832
Sequestration 0.572
Total effectiveness 1.403

Unit: t CO₂‑eq/ha/yr, 100-yr basis

Avoided emissions 1.860
Sequestration 0.344
Total effectiveness 2.204

Unit: t CO₂‑eq/ha/yr, 100-yr basis

Avoided emissions 1.190
Sequestration 0.300
Total effectiveness 1.489
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Cost

We estimated that forest protection costs approximately US$2/t CO₂‑eq (Table 2). Data related to the costs of forest protection are limited, and these estimates are uncertain. The costs of forest protection include up-front costs of land acquisition and ongoing costs of management and enforcement. The market price of land reflects the opportunity cost of not using the land for other purposes (e.g., agriculture or logging). Protecting forests also generates revenue, notably through increased tourism. Costs and revenues vary across regions, depending on the costs of land and enforcement and potential for tourism. 

The cost of land acquisition for ecosystem protection was estimated by Dienerstein et al. (2024), who found a median cost of US$988/ha (range: US$59–6,616/ha), which we amortized over 30 years. Costs of PA maintenance were estimated at US$9–17/ha/yr (Bruner et al., 2004; Waldron et al., 2020). These estimates reflect the costs of effective enforcement and management, but many existing PAs do not have adequate funds for effective enforcement (Adams et al., 2019; Barnes et al., 2018; Burner et al., 2004). Tourism revenues directly attributable to forest protection were estimated to be US$43/ha/yr (Waldron et al., 2020), not including downstream revenues from industries that benefit from increased tourism. Inclusion of a tourism multiplier would substantially increase the estimated economic benefits of forest protection.

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Table 2. Cost per unit of climate impact.

Unit: 2023 US$/t CO₂‑eq, 100-yr basis

median 2
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Learning Curve

A learning curve is defined here as falling costs with increased adoption. The costs of forest protection do not fall with increasing adoption, so there is no learning curve for this solution.

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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as emergency brake, gradual, or delayed.

Protect Forests is an EMERGENCY BRAKE climate solution. It has the potential to deliver a more rapid impact than gradual and delayed solutions. Because emergency brake solutions can deliver their climate benefits quickly, they can help accelerate our efforts to address dangerous levels of climate change. For this reason, they are a high priority.

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Caveats

Additionality, or the degree to which emissions reductions are above and beyond a baseline, is a key caveat for emissions avoided through forest protection (e.g., Fuller et al., 2020; Ruseva et al., 2017). Emissions avoided via forest protection are only considered additional if that forest would have been cleared or degraded without protection (Delacote et al., 2022; Delacote et al., 2024; Gallemore et al., 2020). In this analysis, additionality is addressed by using baseline rates of forest loss outside of PAs in the effectiveness calculation. Additionality is particularly important when forest protection is used to generate carbon offsets. However, the likelihood of forest removal in the absence of protection is often difficult to determine at the local level.

Permanence, or the durability of stored carbon over long timescales, is another important consideration not directly addressed in this solution. Carbon stored in forests can be compromised by natural factors, like drought, heat, flooding, wildfire, pests, and diseases, which are further exacerbated by climate change (Anderegg et al., 2020; Dye et al., 2024). Forest losses via wildfire in particular can create very large pulses of emissions (e.g., Kolden et al. 2024; Phillips et al. 2022) that negate accumulated carbon benefits of forest protection. Reversal of legal protections, illegal forest clearing, biodiversity loss, edge effects from roads, and disturbance from permitted uses can also cause forest losses directly or reduce ecosystem integrity, further increasing vulnerability to other stressors (McCallister et al., 2022).

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Current Adoption

We estimated that approximately 1,673 Mha of forests are currently recognized as PAs or Indigenous peoples’ lands (Table 3e; Garnett et al., 2018; UNEP-WCMC and IUCN, 2024). Using two different maps of global forests that differ in their methodologies and definitions (ESA CCI, 2019; Hansen et al., 2013), we found an upper-end estimate of 1,943 Mha protected and a lower-end estimate of 1,404 Mha protected. These two maps classify forests using different thresholds for canopy cover and vegetation height, different satellite data, and different classification algorithms (see the Appendix for details). 

Based on our calculations, tropical forests make up the majority of forested PAs, with approximately 936 Mha under protection (Table 3d), followed by boreal forests (467 Mha, Table 3a), temperate forests (159 Mha, Table 3b), and subtropical forests (112 Mha, Table 3c). We estimate that 49% of all forests have some legal protection, though only 7% of forests are under strict protection (IUCN class I or II), with the remaining area protected under other IUCN levels, as OECMs, or as Indigenous peoples’ lands.

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Table 3. Current (circa 2023) forest and woodland area under legal protection by biome (Mha). The low and high values are calculated using two different maps of global forest cover that differ in methodology for defining a forest (ESA CCI, 2019; Hansen et al., 2013). Biome-level values may not sum to global totals due to rounding.

Unit: Mha

low 313
mean 467
high 621

Unit: Mha

low 135
mean 159
high 183

Unit: Mha

low 85
mean 112
high 138

Unit: Mha

low 872
mean 936
high 1,000

Unit: Mha

low 1,404
mean 1,673
high 1,943
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Adoption Trend

We calculated the rate of PA expansion based on the year the PA was established. We do not have data on the expansion rate of Indigenous peoples’ lands, so the calculated adoption trend reflects only PAs. An average of 19 Mha of additional forests were protected each year between 2000 and 2020 (Table 4a–e; Figure 1), representing a roughly 2% increase in PAs per year (excluding Indigenous peoples’ lands that are not located in PAs). There were large year-to-year differences in how much new forest area was protected over this period, ranging from only 6.4 Mha in 2020 to over 38 Mha in both 2000 and 2006. Generally, the rate at which forest protection is increasing has been decreasing, with an average increase of 27 Mha/yr between 2000–2010 declining to 11 Mha/yr between 2010–2020. Recent rates of forest protection (2010–2020) are highest in the tropics (5.6 Mha/yr), followed by temperate regions (2.4 Mha/yr) and the boreal (2.0 Mha/yr), and lowest in the subtropics (0.7 Mha/yr).

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Figure 1. Trend in forest protection by climate zone. These values reflect only the area located within PAs; Indigenous peoples’ lands, which were not included in the calculation of the adoption trend, are excluded.

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Table 4. 2000–2020 adoption trend.

Unit: Mha protected/yr

25th percentile 1.3
mean 2.8
median (50th percentile) 2.0
75th percentile 3.4

Unit: Mha protected/yr

25th percentile 1.9
mean 2.8
median (50th percentile) 2.5
75th percentile 3.1

Unit: Mha protected/yr

25th percentile 0.5
mean 1.0
median (50th percentile) 0.7
75th percentile 1.1

Unit: Mha protected/yr

25th percentile 5.4
mean 12.5
median (50th percentile) 7.7
75th percentile 17.8

Unit: Mha protected/yr

25th percentile 9.1
mean 19.0
median (50th percentile) 12.9
75th percentile 25.4
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Adoption Ceiling

We estimated an adoption ceiling of 3,370 Mha of forests globally (Table 5e), defined as all existing forest areas, excluding peatlands and mangroves. Of the calculated adoption ceiling, 469 Mha of boreal forests (Table 5a), 282 Mha of temperate forests (Table 5b), 211 Mha of subtropical forests (Table 5c), and 734 Mha of tropical forests (Table 5d) are currently unprotected. The high and low values represent estimates of currently forested areas from two different maps of forest cover that use different methodologies and definitions (ESA CCI, 2019; Hansen et al., 2013). While it is not socially, politically, or economically realistic that all existing forests could be protected, these values represent the technical upper limit to adoption of this solution. Additionally, some PAs allow for ongoing sustainable use of resources, enabling some demand for wood products to be met via sustainable use of trees in PAs.

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Table 5. Adoption ceiling.

Unit: Mha protected

low 686
mean 936
high 1,186

Unit: Mha protected

low 385
mean 441
high 498

Unit: Mha protected

low 260
mean 323
high 385

Unit: Mha protected

low 1,557
mean 1,669
high 1,782

Unit: Mha protected

low 2,889
mean 3,370
high 3,851
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Achievable Adoption

We defined the lower end of the achievable range for forest protection as all high integrity forests in addition to forests in existing PAs and Indigenous peoples’ lands, totaling 2,297 Mha (Table 6a–e). We estimated that there are 624 Mha of unprotected high integrity forests, based on maps of forest integrity developed by Grantham et al. (2020). High integrity forests have experienced little disturbance from human pressures (i.e., logging, agriculture, and buildings), are located further away from areas of human disturbance, and are well-connected to other forests. High integrity forests are a top priority for protection as they have particularly high value with respect to biodiversity and ecosystem service provisioning. These forests are also not currently being used to meet human demand for land or forest-derived products, and thus their protection may be more feasible. 

To estimate the upper end of the achievable range, we excluded the global areas of planted trees and tree crops from the adoption ceiling (Richter et al., 2024), comprising approximately 335 Mha globally (Table 6a–e). Planted trees include tree stands established for crops such as oil palm, products such as timber and fiber production, and those established as windbreaks or for ecosystem services such as erosion control. These stands are often actively managed and are unlikely to be protected.

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Table 6. Range of achievable adoption levels. 

Unit: Mha protected

Current Adoption 467
Achievable – Low 847
Achievable – High 861
Adoption ceiling 936

Unit: Mha protected

Current Adoption 159
Achievable – Low 204
Achievable – High 378
Adoption ceiling 441

Unit: Mha protected

Current Adoption 112
Achievable – Low 126
Achievable – High 219
Adoption ceiling 323

Unit: Mha protected

Current Adoption 936
Achievable – Low 1,120
Achievable – High 1,577
Adoption ceiling 1,669

Unit: Mha protected

Current Adoption 1,673
Achievable – Low 2,297
Achievable – High 3,035
Adoption ceiling 3,370
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We estimated that forest protection currently avoids approximately 2.00 Gt CO₂‑eq/yr, with potential impacts of 2.49 Gt CO₂‑eq/yr at the low-achievable scenario, 3.62 Gt CO₂‑eq/yr  at the high-achievable scenario, and 4.10 Gt CO₂‑eq/yr at the adoption ceiling (Table 7a–e). Although not directly comparable due to the inclusion of different land covers, these values are aligned with Griscom et al. (2017) estimates that forest protection could avoid 3.6 Gt CO₂‑eq/yr and the IPCC estimate that protection of all ecosystems could avoid 6.2 Gt CO₂‑eq/yr (Nabuurs et al., 2022).

Note that the four adoption scenarios vary only with respect to the area under protection. Increases in either the rate of forest loss that would have occurred if the area had not been protected or in the effectiveness of PAs at avoiding forest loss would substantially increase the climate impacts of forest protection. For instance, a hypothetical 50% increase in the rate of forest loss outside of PAs would increase the carbon impacts of the current adoption, low achievable, high achievable, and adoption ceiling scenarios to 3.0, 3.7, 5.4, and 6.1 Gt CO₂‑eq/yr, respectively. Similarly, if legal forest protection reduced forest loss twice as much as it currently does, the climate impacts of the four scenarios would increase to 3.9, 4.8, 7.0, and 7.8 Gt CO₂‑eq/yr, respectively.

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Table 7. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq/yr, 100-yr basis

Boreal 0.14
Achievable – Low 0.25
Achievable – High 0.26
Adoption ceiling 0.28

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 0.22
Achievable – Low 0.29
Achievable – High 0.53
Adoption ceiling 0.62

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 0.25
Achievable – Low 0.28
Achievable – High 0.48
Adoption ceiling 0.71

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 1.39
Achievable – Low 1.67
Achievable – High 2.35
Adoption ceiling 2.49

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 2.00
Achievable – Low 2.49
Achievable – High 3.62
Adoption ceiling 4.10
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Additional Benefits

Extreme Weather Events

Protected forests are more biodiverse and therefore more resilient and adaptable, providing higher-quality ecosystem services to surrounding communities (Gray et al., 2016). Protected forests can also buffer surrounding areas from the effects of extreme weather events. By increasing plant species richness, forest preservation can contribute to drought and fire tolerance (Buotte et al., 2020). Forests help regulate local climate by reducing temperature extremes (Lawrence et al., 2022). Studies have shown that the extent of forest coverage helps to alleviate vulnerability associated with heat effects (Walton et al., 2016). Tropical deforestation threatens human well-being by removing critical local cooling effects provided by tropical forests, exacerbating extreme heat conditions in already vulnerable regions (Seymour et al., 2022).

Food Security

Protecting forests in predominantly natural areas can improve food security by supporting crop pollination of nearby agriculture. Sarira et al. (2022) found that protecting 58% of threatened forests in Southeast Asia could support the dietary needs of about 305,000–342,000 people annually. Forests also provide a key source of income and livelihoods for subsistence households and individuals (de Souza et al., 2016; Herrera et al., 2017; Naidoo et al., 2019). By maintaining this source of income through forest protection, households can earn sufficient income that contributes to food security. 

Health

Protected forests can benefit the health and well-being of surrounding communities through impacts on the environment and local economies. Herrera et al. (2017) found that in rural areas of low- and middle-income countries, household members living downstream of higher tree cover had a lower probability of diarrheal disease. Proximity to PAs can benefit local tourism, which may provide more economic resources to surrounding households. Naidoo et al. (2019) found that households near PAs in low- and middle-income countries were more likely to have higher levels of wealth and were less likely to have children who were stunted. Reducing deforestation can improve health by lowering vector-borne diseases, mitigating extreme weather impacts, and improving air quality (Reddington et al., 2015). 

Equality

Indigenous peoples have a long history of caring for and shaping landscapes that are rich with biodiversity (Fletcher et al., 2021). Indigenous communities provide vital ecological functions for preserving biodiversity, like seed dispersal and predation (Bliege Bird & Nimmo, 2018). Indigenous peoples also have spiritual and cultural ties to their lands (Garnett et al., 2018). Establishing protected areas must prioritize the return of landscapes to Indigenous peoples so traditional owners can feel the benefits of biodiversity. However, the burden of conservation should not be placed on Indigenous communities without legal recognition or support (Fa et al., 2020). In fact, land grabs and encroachments on Indigenous lands have led to greater deforestation pressure (Sze et al., 2022). Efforts to protect these lands must include legal recognition of Indigenous ownership to support a just and sustainable conservation process (Fletcher et al., 2021).

Nature Protection

Forests are home to a wide range of species and habitats and are essential for safeguarding biodiversity. Forests have high above- and below-ground carbon density, high tree species richness, and often provide habitat to threatened and endangered species (Buotte et al., 2020). PAs can aid in avoiding extinctions by protecting rare and threatened species (Dinerstein et al. 2024). In Southeast Asia, protecting 58% of threatened forests could safeguard about half of the key biodiversity areas in the region (Sarira et al., 2022). 

Water Quality

Forests act as a natural water filter and can maintain and improve water quality (Melo et al., 2021). Forests can also retain nutrients from polluting the larger watershed (Sweeney et al., 2004). For example, forests can uptake excess nutrients like nitrogen, reducing their flow into surrounding water (Sarira et al., 2022). These excessive nutrients can cause eutrophication and algal blooms that negatively impact water quality and aquatic life. 

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Risks

Ecosystem protection initiatives that are not led by or undertaken in close collaboration with local communities can compromise community sovereignty and create injustice and inequity (Baragwanath et al., 2020; Blackman & Viet 2018; Dawson et al., 2024; Fa et al., 2020; FAO, 2024; Garnett et al. 2018; Sze et al. 2022; Tauli-Corpuz et al., 2020). Forest protection has the potential to be a win-win for climate and communities, but only if PAs are established with respect to livelihoods and other socio-ecological impacts, ensuring equity in procedures, recognition, and the distribution of benefits (Zafra-Calvo et al., 2017).

Leakage is a key risk of relying on forest protection as a climate solution. Leakage occurs when deforestation-related activities move outside of PA boundaries, resulting in the relocation of, rather than a reduction in, emissions from forest loss. If forest protection efforts are not coupled with policies to reduce incentives for forest clearing, leakage will likely offset some of the emissions avoided through forest protection. Additional research is needed to comprehensively quantify the magnitude of leakage effects, though two regional-scale studies found only small negative effects (Fuller et al., 2020; Herrera et al., 2019).

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Interactions with Other Solutions

Reinforcing

Other intact and degraded ecosystems often occur within areas of forest protection. Therefore, forest protection can facilitate natural restoration of these other degraded ecosystems, and increase the health of adjacent ecosystems.

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Reducing the demand for agricultural land will reduce barriers to forest protection.

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Competing

Forest protection will decrease the availability and increase the prices of wood feedstocks for other applications.

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Dashboard

Solution Basics

ha protected

t CO₂-eq (100-yr)/unit/yr
0.299
units
Current 4.67×10⁸ 08.47×10⁸8.61×10⁸
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.14 0.250.26
US$ per t CO₂-eq
2
Emergency Brake

CO₂

Solution Basics

ha protected

t CO₂-eq (100-yr)/unit/yr
1.403
units
Current 1.59×10⁸ 02.04×10⁸3.78×10⁸
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.22 0.290.53
US$ per t CO₂-eq
2
Emergency Brake

CO₂

Solution Basics

ha protected

t CO₂-eq (100-yr)/unit/yr
2.204
units
Current 1.12×10⁸ 01.26×10⁸2.19×10⁸
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.25 0.280.48
US$ per t CO₂-eq
2
Emergency Brake

CO₂

Solution Basics

ha protected

t CO₂-eq (100-yr)/unit/yr
1.489
units
Current 9.36×10⁸ 01.12×10⁹1.577×10⁹
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 1.39 1.672.35
US$ per t CO₂-eq
2
Emergency Brake

CO₂

% tree cover
0100

Tree cover, 2000 (excluding mangroves and peatlands)

We exclude mangroves and peatlands because they are addressed in other solutions.

Global Forest Watch (2023). Global peatlands [Data set]. Retrieved December 6, 2024 from Link to source: https://data.globalforestwatch.org/datasets/gfw::global-peatlands/about

Hansen, M.C., Potapov, P.V., Moore, R., Hancher, M., Turubanova, S.A., Tyukavina, A., Thau, D., Stehman, S.V., Goetz, S.J., Loveland, T.R., Kommareddy, A., Egorov, A., Chini, L., Justice, C.O., and Townshend, J.R.G. (2013). High-resolution global maps of 21st-century forest cover change [Data set]. Science 342 (15 November): 850-53. Link to source: https://glad.earthengine.app/view/global-forest-change

UNEP-WCMC (2025). Ocean+ habitats (version 1.3) [Data set]. Retrieved November 2024 from habitats.oceanplus.org

% tree cover
0100

Tree cover, 2000 (excluding mangroves and peatlands)

We exclude mangroves and peatlands because they are addressed in other solutions.

Global Forest Watch (2023). Global peatlands [Data set]. Retrieved December 6, 2024 from Link to source: https://data.globalforestwatch.org/datasets/gfw::global-peatlands/about

Hansen, M.C., Potapov, P.V., Moore, R., Hancher, M., Turubanova, S.A., Tyukavina, A., Thau, D., Stehman, S.V., Goetz, S.J., Loveland, T.R., Kommareddy, A., Egorov, A., Chini, L., Justice, C.O., and Townshend, J.R.G. (2013). High-resolution global maps of 21st-century forest cover change [Data set]. Science 342 (15 November): 850-53. Link to source: https://glad.earthengine.app/view/global-forest-change

UNEP-WCMC (2025). Ocean+ habitats (version 1.3) [Data set]. Retrieved November 2024 from habitats.oceanplus.org

Maps Introduction

The adoption, potential adoption, and effectiveness of forest protection are highly geographically variable. While forest protection can help avoid emissions anywhere that forests occur, areas with high rates of forest loss from human drivers and particularly carbon-rich forests have the greatest potential for avoiding emissions via forest protection. The tropics and subtropics are high-priority areas for forest protection as they contain 55% of currently unprotected forest area, forest loss due to agricultural expansion is particularly concentrated in these regions (Curtis et al., 2018; West et al., 2014; Gibbs et al., 2010), and tend to have larger biomass carbon stocks than boreal forests (Harris et al., 2021). 

Developed countries also have significant potential to protect remaining old and long unlogged forests and foster recovery in secondary natural forests. The top 10 forested countries include Canada, the USA, Russia and even Australia, with the latter moving towards ending commodity production in its natural forests and increasing formal protection. Restoration of degraded forests is addressed in the Forest Restoration solution, but including regenerating forests in well designed protected areas is well within the capacity of every developed country.

Buffering and reconnecting existing high integrity forests is a low risk climate solution that increases current and future forest ecosystem resilience and adaptive capacity (Brennan et al., 2022; Brink et al., 2017; Grantham et al., 2020; Rogers et al., 2022). Forests with high ecological integrity provide outsized benefits for carbon storage and biodiversity and have greater resilience, making them top priorities for protection (Grantham et al., 2020; Rogers et al., 2022). Within a given forest, large-diameter trees similarly provide outsized carbon storage and biodiversity benefits, comprising only 1% of trees globally but storing 50% of the above ground forest carbon (Lutz et al., 2018). Additionally, forests that improve protected area connectivity (Brennan et al., 2022; Brink et al., 2017), areas at high risk of loss (particularly to expansion of commodity agriculture; Curtis et al., 2018; Hansen et al., 2013), and areas with particularly large or specialized benefits for biodiversity, ecosystem services, and human well-being (Dinerstein et al., 2024; Sarira et al., 2022; Soto-Navarro et al., 2020) may be key targets for forest protection.

Action Word
Protect
Solution Title
Forests
Classification
Highly Recommended
Lawmakers and Policymakers
  • Set achievable targets and pledges for PA designation and set clear effectiveness goals for PAs, emphasizing the effectiveness of current PAs before seeking to expand designations.
  • Use a variety of indicators to measure effectiveness, such as estimated avoided deforestation.
  • Ensure public procurement utilizes deforestation-free products and supply chains.
  • Grant Indigenous communities full property rights and autonomy and support them in monitoring, managing, and enforcing PAs.
  • Ensure PAs do not displace, violate rights, or reduce access to vital resources for local and Indigenous communities.
  • Invest in PA infrastructure, monitoring, management, and enforcement mechanisms.
  • Utilize real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Join, support, or create certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Conduct proactive land-use planning to avoid roads and other development projects that may interfere with PAs or incentivize deforestation.
  • Create processes for legal grievances, dispute resolution, and restitution.
  • Remove harmful agricultural and logging subsidies.
  • Prioritize reducing food loss and waste.
  • Create education programs that educate the public on PA regulations, the benefits of the regulations, and how to use forest resources sustainably.

Further information:

Practitioners
  • Set achievable targets and pledges for PA designation and set clear effectiveness goals for PAs, emphasizing the effectiveness of current PAs before seeking to expand designations
  • Use a variety of indicators to measure effectiveness, such as estimated avoided deforestation.
  • Ensure PAs do not displace, violate rights, or reduce access to vital resources for local and Indigenous communities.
  • Utilize real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Create sustainable use regulations for PA areas that provide resources to the local community.
  • Conduct proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Grant Indigenous communities full property rights and autonomy and support them in monitoring, managing, and enforcing PAs.
  • Join, support, or create certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Create processes for legal grievances, dispute resolution, and restitution.
  • Create education programs that educate the public on PA regulations, the benefits of the regulations, and how to use forest resources sustainably.

Further information:

Business Leaders
  • Create deforestation-free supply chains, utilizing data, information, and the latest technology to inform product sourcing.
  • Integrate deforestation-free business and investment policies and practices in Net-Zero strategies.
  • Only purchase carbon credits from high-integrity, verifiable carbon markets and do not use them as replacements for reducing emissions.
  • Help shift the public narrative around carbon markets as integrity increases to boost education, dialogue, and awareness.
  • Develop financial instruments to invest in PA jurisdictions, focusing on supporting Indigenous communities.
  • Join or create public-private partnerships, alliances, or coalitions of stakeholders and rightsholders to support PAs and advance deforestation-free markets.
  • Join, support, or create certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Conduct proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for public relations and communications.
  • Support education programs that educate the public on PA regulations, the benefits of the regulations, and how to use forest resources sustainably.
  • Leverage political influence to advocate for stronger PA policies at national and international levels, especially policies that reduce deforestation pressure. 

Further information:

Nonprofit Leaders
  • Ensure operations utilize deforestation-free products and supply chains.
  • Advocate for PAs and for public investments and evaluation indicators to strengthen the effectiveness of PAs.
  • Assist in managing and monitoring PAs, utilizing real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Provide financial support for PAs management, monitoring, and enforcement.
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Advocate for creating legal grievance processes, dispute resolution mechanisms, and restitution procedures for violations or disagreements over PAs.
  • Support high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Help shift the public narrative around carbon markets as integrity increases to boost education, dialogue, and awareness.
  • Support PAs, businesses, and investors by sharing data, information, and investment frameworks that successfully avoid deforestation.
  • Help shift public narratives to mobilize public action and build political will for PAs by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Join, support, or create certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for legal protection and public relations.
  • Advocate for non-timber forest products to support local and Indigenous communities.
  • Advocate to remove harmful agricultural subsidies and prioritize reducing food loss and waste.

Further information:

Investors
  • Create deforestation-free investment portfolios, utilizing data, information, and the latest technology to inform investments.
  • Invest in PA infrastructure, monitoring, management, and enforcement mechanisms.
  • Invest in green bonds or high-integrity carbon credits for forest conservation efforts.
  • Develop financial instruments to invest in PA jurisdictions, focusing on supporting Indigenous communities.
  • Support PAs, other investors, and NGOs by sharing data, information, and investment frameworks that successfully avoid investments that drive deforestation.
  • Join, support, or create science-based certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Help shift public narratives to mobilize public action and build political will for PAs by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Require portfolio companies to eliminate deforestation from their supply chains and ask that they demonstrate strong PA practices.
  • Consider opportunities to invest in forest monitoring technologies or bioeconomy products derived from standing forests (e.g., nuts, berries, or other derivatives)

Further information:

Philanthropists and International Aid Agencies
  • Ensure operations utilize deforestation-free products and supply chains.
  • Provide financial support for PAs management, monitoring, and enforcement.
  • Assist in monitoring PAs, utilizing real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Support and finance high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Help shift the public narrative around carbon markets as integrity increases to boost education, dialogue, and awareness.
  • Support PAs, businesses, and investors by sharing data, information, and investment frameworks that successfully avoid deforestation.
  • Help shift public narratives to mobilize public action and build political will for PAs by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Invest in and support Indigenous and local communities' capacity for public relations and communications.
  • Financially support Indigenous land tenure.
  • Join, support, or create certification schemes like the Forest Stewardship Council for sustainable logging practices.
  • Advocate for PAs and for public investments and evaluation indicators to strengthen the effectiveness of PAs.
  • Advocate for legal grievances, dispute resolution, and restitution processes.

Further information:

Thought Leaders
  • Advocate for PAs and for public investments and evaluation indicators to strengthen the effectiveness of PAs.
  • Assist in monitoring PAs, utilizing real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Advocate for legal grievances, dispute resolution, and restitution processes.
  • Support high-integrity carbon markets, institutions, rules, and norms to cultivate the demand for high-quality carbon credits.
  • Help shift the public narrative around carbon markets as integrity increases to boost education, dialogue, and awareness.
  • Support PAs, businesses, and investors by sharing data, information, and investment frameworks that successfully avoid deforestation.
  • Help shift public narratives to mobilize public action and build political will for PAs by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Amplify the voices of local communities and civil society to promote robust media coverage.
  • Support Indigenous and local communities' capacity for public relations and communications.

Further information:

Technologists and Researchers
  • Improving PA monitoring methods and data collection, utilizing satellite imagery and GIS tools.
  • Develop land-use planning tools that help avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Create tools for local communities to monitor PAs, such as mobile apps, e-learning platforms, and mapping tools.
  • Conduct evaluations of the species richness of potential PAs and recommend areas of high biodiversity to be designated as PAs.
  • Develop verifiable carbon credits using technology such as blockchain to improve the integrity of carbon markets.
  • Develop supply chain tracking software for investors and businesses seeking to create deforestation-free portfolios and products.

Further information:

Communities, Households, and Individuals
  • Ensure purchases and investments utilize deforestation-free products and supply chains.
  • Advocate for PAs and for public investments and evaluation indicators to strengthen the effectiveness of PAs.
  • Assist in monitoring PAs, utilizing real-time monitoring and satellite data such as the “Real-Time System for Detection of Deforestation” (DETER).
  • Assist in conducting proactive land-use planning to avoid infrastructure or development projects that may interfere with PAs or incentivize deforestation.
  • Advocate for legal grievances, dispute resolution, and restitution processes.
  • Support Indigenous and local communities' capacity for public relations and communications.
  • Assist with evaluations of the species richness of potential PAs and advocate for PAs in areas of high biodiversity that are threatened.
  • Help shift public narratives to mobilize public action and build political will for PAs by creating educational campaigns and strengthening networks of stakeholders and rightsholders.
  • Undertake forest protection and expansion initiatives locally by working to preserve existing forests and restore degraded forest areas.
  • Engage in citizen science initiatives by partnering with researchers or conservation groups to monitor PAs and document threats. 

Further information:

Sources
Evidence Base

There is high scientific consensus that forest protection is a key strategy for reducing forest loss and addressing climate change. Rates of forest loss are lower inside of PAs and Indigenous peoples’ lands than outside of them. Globally, Wolf et al. (2021) found that rates of forest loss inside PAs are 40.5% lower on average than in unprotected areas, and Li et al. (2024) estimated that overall forest loss is 14% lower in PAs relative to unprotected areas. Regional studies find similar average effects of PAs on deforestation rates. For instance, McNichol et al. (2023) reported 39% lower deforestation rates in African woodlands in PAs relative to unprotected areas, and Graham et al. (2021) reported 69% lower deforestation rates in PAs relative to unprotected areas in Southeast Asia. In the tropics, Sze et al. (2022) found that rates of forest loss were similar between Indigenous lands and PAs, with forest loss rates reduced 17–29% relative to unprotected areas. Baragwanath & Bayi (2020) reported a 75% decline in deforestation in the Brazilian Amazon when Indigenous peoples are granted full property rights.

Reductions in forest loss lead to proportionate reductions in CO₂ emissions. The Intergovernmental Panel on Climate Change (IPCC) estimated that ecosystem protection, including forests, peatlands, grasslands, and coastal wetlands, has a technical mitigation potential of 6.2 Gt CO₂‑eq/yr, 4.0 Gt of which are available at a carbon price less than US$100 tCO₂‑eq/yr  (Nabuurs et al., 2022). Similarly, Griscom et al. (2017) found that avoiding human-caused forest loss is among the most effective natural climate solutions, with a potential impact of 3.6 Gt CO₂‑eq/yr (including forests on peatlands), nearly 2 Gt CO₂‑eq/yr of which is achievable at a cost below US$10/t CO₂‑eq/yr.

The results presented in this document were produced through analysis of 12 global datasets. We recognize that geographic biases can influence the development of global datasets and hope this work inspires research and data sharing on this topic in underrepresented regions.

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Appendix

In this analysis, we integrated global land cover data, maps of forest loss rates, shapefiles of PAs and Indigenous people’s lands, country-scale data on reductions in forest loss inside of PAs, and biome-scale data on forest carbon stocks and sequestration rates to calculate currently protected forest area, total global forest area, and avoided emissions from forest protection. Forested peatlands and mangroves are excluded from this analysis and addressed in the Protect Peatlands and Protect Coastal Wetlands solutions, respectively.

Land cover data

We used two land cover data products to estimate forest extent inside and outside of PAs and Indigenous people’s lands, including: 1) the Global Forest Watch (GFW) tree cover dataset (Hansen et al., 2013), resampled to 30 second resolution, and 2) the 2022 European Space Agency Climate Change Initiative (ESA CCI) land cover dataset at native resolution (300 m). For the ESA CCI dataset, all non-flooded tree cover classes (50, 60, 70, 80, 90) and the “mosaic tree and shrub (>50%)/herbaceous cover (<50%)” class (100) and associated subclasses were included as forests. Both products are associated with uncertainty, which we did not address directly in our calculations. We include estimates from both products in order to provide readers with a sense of the variability in values that can stem from different land cover classification methods, which are discussed in more detail below.

These two datasets have methodological differences that result in substantially different classifications of forest extent, including their thresholds for defining forests, their underlying satellite data, and the algorithms used to classify forests based on the satellite information. For example, the ESA CCI product classifies 300-meter pixels with >15% tree cover as forests (based on our included classes), attempts to differentiate tree crops, relies on a 2003–2012 baseline land cover map coupled with a change-detection algorithm, and primarily uses imagery from MERIS, PROBA-V, and Sentinel missions (ESA CCI 2019). In contrast, the Global Forest Watch product generally requires >30% tree cover at 30-meter resolution, does not exclude tree crops, relies on a regression tree model for development of a baseline tree cover map circa 2010, and primarily uses Landsat ETM+ satellite imagery (Hansen et al., 2013). We recommend that interested readers refer to the respective user guides for each data product for a comprehensive discussion of the complex methods used for their development.

We used the Forest Landscape Integrity Index map developed by Grantham et al. (2020), which classifies forests with integrity indices ≥9.6 as high integrity. These forests are characterized by minimal human disturbance and high connectivity. Mangroves and peatlands were excluded from this analysis. We used a map of mangroves from Giri et al. (2011) and a map of peatlands compiled by Global Forest Watch to define mangrove and peatland extent (accessed at https://data.globalforestwatch.org/datasets/gfw::global-peatlands/about). The peatlands map is a composite of maps from five publications: Crezee et al. (2022), Gumbricht et al. (2017), Hastie et al. (2022), Miettinen et al. (2016), and Xu et al. (2018). For each compiled dataset, the data were resampled to 30-second resolution by calculating the area of each grid cell occupied by mangroves or peatlands. For each grid cell containing forests, the “eligible” forest area was calculated by subtracting the mangrove and peatland area from the total forest area for each forest cover dataset (GFW, ESA CCI, and high-integrity forests).

Protected forest areas

We identified protected forest areas using the World Database on Protected Areas (WDPA, 2024), which contains boundaries for each PA and additional information, including their establishment year and IUCN management category (Ia to VI, not applicable, not reported, and not assigned). For each PA polygon, we extracted the forest area from the GFW, ESA CCI, and high-integrity dataset (after removing the peatland and mangrove areas).

Each protected area was classified into a climate zone based on the midpoint between its minimum and maximum latitude. Zones included tropical (23.4°N–23.4°S), subtropical (23.4°–35° latitude), temperate (35°–50° latitude), and boreal (>50° latitude) in order to retain some spatial variability in emissions factors. We aggregated protected forest cover areas (from each of the two forest cover datasets and the high-integrity forest data) by IUCN class and climate zone. To evaluate trends in adoption over time, we also aggregated protected areas by establishment year. We used the same method to calculate the forest area that could be protected, extracting the total area of each land cover type by climate zone (inside and outside of existing PAs). 

We used maps from Garnett et al. (2018) to identify Indigenous people’s lands that were not inside established PAs. We calculated the total forest area within Indigenous people’s lands (excluding PAs, mangroves, and peatlands) using the same three forest area data sources. 

Forest loss and emissions factors

Forest loss rates were calculated for unprotected areas using the GFW forest loss dataset for 2001–2022, resampled to 1 km resolution. Forest losses were reclassified according to their dominant drivers based on the maps originally developed by Curtis et al. (2018), with updates accessible through GFW. Dominant drivers of forest loss include commodity agriculture, shifting agriculture, urbanization, forestry, and wildfire. We classified all drivers except wildfire as human-caused forest loss for this analysis. We calculated the area of forest loss attributable to each driver within each climate zone, which represented the “baseline” rate of forest loss outside of PAs. 

To calculate the difference in forest loss rates attributable to protection, we used country-level data from Wolf et al. (2021) on the ratio of forest loss in unprotected areas versus PAs, controlling for a suite of socio-environmental characteristics. We classified countries into climate zones based on their median latitude and averaged the ratios within climate zones. We defined the avoided forest loss attributable to protection as the product of the baseline forest loss rate and the ratio of forest loss outside versus inside of PAs.

We calculated the carbon benefits of avoided forest loss by multiplying avoided forest loss by average forest carbon stocks and sequestration rates. Harris et al. (2021) reported carbon stocks and sequestration rates by climate zone (boreal, temperate, subtropical, and tropical), and forest type. Carbon stocks and sequestration rates for primary and old secondary (>20 years old) forests were averaged for this analysis. We calculated carbon sequestration over a 20-yr period to provide values commensurate with the one-time loss of biomass carbon stocks.

Source data

Crezee, B. et al. Mapping peat thickness and carbon stocks of the central Congo Basin using field data. Nature Geoscience 15: 639-644 (2022). https://www.nature.com/articles/s41561-022-00966-7. Data downloaded from https://congopeat.net/maps/, using classes 4 and 5 only (peat classes). 

Curtis, P. G., Slay, C. M., Harris, N. L., Tyukavina, A., & Hansen, M. C. (2018). Classifying drivers of global forest loss. Science, 361(6407), 1108–1111. https://doi.org/10.1126/science.aau3445

ESA CCI (2019). Copernicus Climate Change Service, Climate Data Store: Land cover classification gridded maps from 1992 to present derived from satellite observation. Copernicus Climate Change Service (C3S) Climate Data Store (CDS). Accessed November 2024. doi: 10.24381/cds.006f2c9a

Garnett, S. T., Burgess, N. D., Fa, J. E., Fernández-Llamazares, Á., Molnár, Z., Robinson, C. J., Watson, J. E. M., Zander, K. K., Austin, B., Brondizio, E. S., Collier, N. F., Duncan, T., Ellis, E., Geyle, H., Jackson, M. V., Jonas, H., Malmer, P., McGowan, B., Sivongxay, A., & Leiper, I. (2018). A spatial overview of the global importance of Indigenous lands for conservation. Nature Sustainability, 1(7), 369–374. https://doi.org/10.1038/s41893-018-0100-6

Giri C, Ochieng E, Tieszen LL, Zhu Z, Singh A, Loveland T, Masek J, Duke N (2011). Status and distribution of mangrove forests of the world using earth observation satellite data (version 1.3, updated by UNEP-WCMC). Global Ecology and Biogeography 20: 154-159. doi: 10.1111/j.1466-8238.2010.00584.x . Data URL: http://data.unep-wcmc.org/datasets/4

Gumbricht, T. et al. An expert system model for mapping tropical wetlands and peatlands reveals South America as the largest contributor. Global Change Biology 23, 3581–3599 (2017). https://onlinelibrary.wiley.com/doi/full/10.1111/gcb.13689 

Hansen, M. C., Potapov, P. V., Moore, R., Hancher, M., Turubanova, S. A., Tyukavina, A., Thau, D., Stehman, S. V., Goetz, S. J., Loveland, T. R., Kommareddy, A., Egorov, A., Chini, L., Justice, C. O., & Townshend, J. R. G. (2013). High-Resolution Global Maps of 21st-Century Forest Cover Change. Science, 342(6160), 850–853. https://doi.org/10.1126/science.1244693. Data available on-line from: http://earthenginepartners.appspot.com/science-2013-global-forest. Accessed through Global Forest Watch on 01/12/2024. www.globalforestwatch.org

Harris, N. L., Gibbs, D. A., Baccini, A., Birdsey, R. A., de Bruin, S., Farina, M., Fatoyinbo, L., Hansen, M. C., Herold, M., Houghton, R. A., Potapov, P. V., Suarez, D. R., Roman-Cuesta, R. M., Saatchi, S. S., Slay, C. M., Turubanova, S. A., & Tyukavina, A. (2021). Global maps of twenty-first century forest carbon fluxes. Nature Climate Change, 11(3), 234–240. https://doi.org/10.1038/s41558-020-00976-6

Hastie, A. et al. Risks to carbon storage from land-use change revealed by peat thickness maps of Peru. Nature Geoscience 15: 369-374 (2022). https://www.nature.com/articles/s41561-022-00923-4

Miettinen, J., Shi, C. & Liew, S. C. Land cover distribution in the peatlands of Peninsular Malaysia, Sumatra and Borneo in 2015 with changes since 1990. Global Ecological Conservation. 6, 67– 78 (2016). https://www.sciencedirect.com/science/article/pii/S2351989415300470

UNEP-WCMC and IUCN (2024), Protected Planet: The World Database on Protected Areas (WDPA) and World Database on Other Effective Area-based Conservation Measures (WD-OECM) [Online], Accessed November 2024, Cambridge, UK: UNEP-WCMC and IUCN. Available at: www.protectedplanet.net.

Wolf, C., Levi, T., Ripple, W. J., Zárrate-Charry, D. A., & Betts, M. G. (2021). A forest loss report card for the world’s protected areas. Nature Ecology & Evolution, 5(4), 520–529. https://doi.org/10.1038/s41559-021-01389-0

Xu et al. PEATMAP: Refining estimates of global peatland distribution based on a meta-analysis. CATENA 160: 134-140 (2018). https://www.sciencedirect.com/science/article/pii/S0341816217303004 

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Updated Date

Reduce Food Loss & Waste

Submitted by Drawdown Admin on
Sector
Food, Agriculture, Land & Ocean
Mode
Cut Emissions
Cluster
Curb Growing Demands
Image
Peatland
Coming Soon
On
Summary

More than one-third of all food produced for human consumption is lost or wasted before it can be eaten. This means that the GHGs emitted during the production and distribution of that particular food – including emissions from agriculture-related deforestation and soil management, methane emissions from livestock and rice production, and nitrous oxide emissions from fertilizer management – are also wasted. This solution reduces emissions by lowering the amount of food and its associated emissions that are lost or wasted across the supply chain, from production through consumption.

Extreme weather events
Income & work,Food security,Health
Land resources,Water resources
Description for Social and Search
Reduce Food Loss and Waste is a Highly Recommended climate solution. It avoids the embodied greenhouse gas emissions in food that is lost or wasted across the supply chain, from production through consumers.
Overview

The global food system, including land use, production, storage, and distribution, generates more than 25% of global GHG emissions (Poore and Nemecek, 2018). More than one-third of this food is lost or wasted before it can be eaten, with estimated associated emissions being recorded at 4.9 Gt CO₂‑eq/yr (our own calculation). FLW emissions arise from supply chain embodied emissions (i.e., the emissions generated from producing food and delivering to consumers). Reducing food loss and waste helps avoid the embodied emissions while simultaneously increasing food supply and reducing pressure to expand agricultural land use and intensity.

FLW occurs at each stage of the food supply chain (Figure 1). Food loss refers to the stages of production, handling, storage, and processing within the supply chain. Food waste occurs at the distribution, retail, and consumer stages of the supply chain.

Figure 1. GHG emissions occur at each stage of the food supply chain. Food loss occurs at the pre-consumer stages of the supply chain, whereas food waste occurs at the distribution, market, and consumption stages. Credit: Project Drawdown

Diagram showing five stages: Production, Handling and Storage, Processing, Distribution and Market, and Consumption, with Loss occurring in the first three stages, and waste occurring in the last two stages.

Food loss can be reduced through improved post-harvest management practices, such as increasing the number and storage capacity of warehouses, optimizing processes and equipment, and improving packaging to increase shelf life. Retailers can reduce food waste by improving inventory management, forecasting demand, donating unsold food to food banks, and standardizing date labeling. Consumers can reduce food waste by educating themselves, making informed purchasing decisions, and effectively planning meals. The type of interventions to reduce FLW will depend on the type(s) of food product, the supply chain stage(s), and the location(s). 

When FLW cannot be prevented, organic waste can be managed in ways that limit its GHG emissions. Waste management is not included in this solution but is addressed in other Drawdown Explorer solutions (see Deploy Methane Digesters, Improve Landfill Management, and Increase Composting).

Almaraz, M., Houlton, B. Z., Clark, M., Holzer, I., Zhou, Y., Rasmussen, L., Moberg, E., Manaigo, E., Halpern, B. S., Scarborough, C., Lei, X. G., Ho, M., Allison, E., Sibanda, L., & Salter, A. (2023). Model-based scenarios for achieving net negative emissions in the food system. PLOS Clim 2(9). Link to source: https://doi.org/10.1371/journal.pclm.0000181

Amicarelli, V., Lagioia, G., & Bux, C. (2021). Global warming potential of food waste through the life cycle assessment: An analytical review. Environmental Impact Assessment Review, 91. Link to source: https://doi.org/10.1016/j.eiar.2021.106677

Anríquez, G., Foster, W., Santos Rocha, J., Ortega, J., Smolak, J., & Jansen, S. (2023). Reducing food loss and waste in the Near East and North Africa – Producers, intermediaries and consumers as key decision-makers. FAO. Link to source: https://doi.org/10.4060/cc3409en

Babiker, M., Blok, K., Cohen, B., Cowie, A., Geden, O., Ginzburg, V., Leip, A., Smith, P., Sugiyama, M., & Yamba, F. (2023). Cross-sectoral perspectives. In Shukla, P.R, and Skea, J., (Eds.), IPCC, 2022: Climate Change 2022: Mitigation of Climate Change (pp. 1235–1354). Cambridge University Press. Link to source: https://www.ipcc.ch/report/ar6/wg3/downloads/report/IPCC_AR6_WGIII_Chapter12.pdf 

Byrne, F., Medina, M. K., Mosqueda, E., Salinas, E., Suarez Peña, A. C., Suarez, J. D., Raimondi, G., & Molina, M. (2024). Sustainability Impacts of Food Recovery & Redistribution Organizations. The Global FoodBanking Network. Link to source: https://www.foodbanking.org/resources/frame-methodology/

Cattaneo, A., Federighi, G., & Vaz, S. (2021). The environmental impact of reducing food loss and waste: A critical assessment. Food Policy, 98. Link to source: https://doi:10.1016/j.foodpol.2020.101890

Cattaneo, A., Sánchez, M. V., Torero, M., & Vos, R. (2021). Reducing food loss and waste: Five challenges for policy and research. Food Policy, 98. Link to source: https://doi.org/10.1016/j.foodpol.2020.101974

Chen, C., Chaudhary, A., & Mathys, A. (2020). Nutritional and environmental losses embedded in global food waste. Resources, Conservation and Recycling, 160. Link to source: https://doi.org/10.1016/j.resconrec.2020.104912

Creutzig, F., Niamir, L., Bai, X., Callaghan, M., Cullen, J., Díaz-José, J, Figueroa, M., Grubler, A., Lamb, W.F., Leip, A., Masanet, E., Mata, É., Mattauch, L., Minx, J., Mirasgedis, S., Mulugetta, Y., Nugroho, S.B., Pathak, M., Perkins, P., Roy, J., de la Rue du Can, S., Saheb, Y., Some, S., Steg, L., Steinberger, J., & Ürge-Vorsatz, D. (2021). Demand-side solutions to climate change mitigation consistent with high levels of well-being. Nature Climate Change, 12(1): 36-46. Link to source: https://doi.org/10.1038/s41558-021-01219-y 

Crippa, M., Solazzo, E., Guizzardi, D., Monforti-Ferrario, F., Tubiello, F. N., & Leip, A. (2021). Food systems are responsible for a third of global anthropogenic GHG emissions. Nature Food, 2(3): 198-209. Link to source: https://doi.org/10.1038/s43016-021-00225-9

Davidenko, V., & Sweitzer, M. (2024). U.S. households that earn less spend a higher share of income on food. USDA Economic Research Service. Link to source: https://www.ers.usda.gov/data-products/charts-of-note/chart-detail?chartId=110391#:~:text=U.S.%20households%20were%20divided%20into,32.6%20percent%20of%20their%20income 

de Gorter, H., Drabik, D., Just, D. R., Reynolds, C., & Sethi, G. (2021). Analyzing the economics of food loss and waste reductions in a food supply chain. Food Policy, 98. Link to source: https://doi.org/10.1016/j.foodpol.2020.101953

Delgado, L., Schuster, M., & Torero, M. (2021). Quantity and quality food losses across the value chain: A comparative analysis. Food Policy, 98. Link to source: https://doi.org/10.1016/j.foodpol.2020.101958

Eurostat (2024). Food waste and food waste prevention by NACE Rev. 2 activity [Dataset]. Link to source: https://ec.europa.eu/eurostat/databrowser/view/env_wasfw/default/table?lang=en&category=env.env_was.env_wasst 

European Commission Knowledge Center for Bioeconomy (2024). EU Bioeconomy Monitoring System [Dataset]. Link to source: https://knowledge4policy.ec.europa.eu/bioeconomy/monitoring_en 

Fabi, C., Cachia, F., Conforti, P., English, A., & Rosero Moncayo, J. (2021). Improving data on food losses and waste: From theory to practice. Food Policy, 98. Link to source: https://doi.org/10.1016/j.foodpol.2020.101934

Food and Agriculture Organization of the United Nations. (2014) Food wastage footprint: Full-cost accounting. Food and Agriculture Organization of the United Nations. Link to source: https://openknowledge.fao.org/server/api/core/bitstreams/6a266c4f-8493-471c-ab49-30f2e51eec8c/content

Food and Agriculture Organization of the United Nations. (2019). The State of Food and Agriculture 2019: Moving forward on food loss and waste reduction. Food and Agriculture Organization of the United Nations. Link to source: https://openknowledge.fao.org/server/api/core/bitstreams/11f9288f-dc78-4171-8d02-92235b8d7dc7/content

Food and Agriculture Organization of the United Nations. (2023). Tracking progress on food and agriculture-related SDG indicators 2023. Rome: Link to source: https://doi.org/10.4060/cc7088en

Food Waste Coalition of Action. (2024). Driving Emissions Down and Profit Up by Reducing Food Waste. The Consumer Goods Forum and AlixPartners. Retrieved from Link to source: https://www.theconsumergoodsforum.com/wp-content/uploads/2024/06/Driving-Emissions-Down-Profit-Up-By-Reducing-Food-Waste-FWReport2024-1.pdf 

Gatto, A., & Chepeliev, M. (2024). Reducing global food loss and waste could improve air quality and lower the risk of premature mortality. Environmental Research Letters, 19(1). Link to source: https://doi.org/10.1088/1748-9326/ad19ee 

Goossens, Y., Wegner, A., & Schmidt, T. (2019). Sustainability assessment of food waste prevention measures: Review of existing evaluation practices. Frontiers in Sustainable Food Systems, 3. Link to source: https://doi.org/10.3389/fsufs.2019.00090 

Guo, X., Broeze, J., Groot, J. J., Axmann, H., & Vollebregt, M. (2020). A worldwide hotspot analysis on food loss and waste, associated greenhouse gas emissions, and protein losses. Sustainability, 12(18). https://doi.org/10.3390/su12187488

Hanson, C., & Mitchell, P. (2017). The Business Case for Reducing Food Loss and Waste. Link to source: https://champions123.org/sites/default/files/2020-08/business-case-for-reducing-food-loss-and-waste.pdf

Hanson, C., Flanagan, K., Robertson, K., Axmann, H., Bos-Brouwers, H., Broeze, J., Kneller, C., Maier, D., McGee, C., O’Connor, C., Sonka, S., Timmermans, T., Vollebregt, M., Westra, E. (2019). Reducing Food Loss and Waste: Ten Interventions to Scale Impact. Washington DC: World Resources Institute. Retrieved from: Link to source: https://www.wri.org/reducing-food-loss-and-waste-ten-interventions-scale-impact

Hegnsholt, E., Unnikrishnan, S., Pollmann-Larsen, M., Askelsdottir, B., & Gerard, M. (2018). Tackling the 1.6-billion-ton food loss and waste crisis. The Boston Consulting Group, Food Nation, State of Green. Link to source: https://web-assets.bcg.com/img-src/BCG-Tackling-the-1.6-Billion-Ton-Food-Waste-Crisis-Aug-2018%20%281%29_tcm9-200324.pdf

Hegwood, M., Burgess, M. G., Costigliolo, E. M., Smith, P., Bajzelj, B., Saunders, H., & Davis, S. J. (2023). Rebound effects could offset more than half of avoided food loss and waste. Nat Food, 4(7): 585-595. Link to source: https://doi.org/10.1038/s43016-023-00792-z 

Jaglo, K., Kelly, S., & Stephenson, J. (2021). From Farm to Kitchen: The Environmental Impacts of U.S. Food Waste. US Environmental Protection Agency. Link to source: https://www.epa.gov/land-research/farm-kitchen-environmental-impacts-us-food-waste 

Karl, K., Tubiello, F. N., Crippa, M., Poore, J., Hayek, M. N., Benoit, P., Chen, M., Corbeels, M., Flammini, A., Garland, S., Leip, A., McClelland, S., Mencos Contreras, E., Sandalow, D., Quadrelli, R., Sapkota, T., and Rosenzweig, C. (2024). Harmonizing food systems emissions accounting for more effective climate action. Environmental Research: Food Systems, 2(1). Link to source: https://doi.org/10.1088/2976-601X/ad8fb3 

Kenny, S. (2025). Estimating the Cost of Food Waste to American Consumers. (No. EPA/600/R25-048). U.S. Environmental Protection Agency Office of Research and Development. Link to source: https://www.epa.gov/system/files/documents/2025-04/costoffoodwastereport_508.pdf 

Kenny, S., Stephenson, J., Stern, A., Beecher, J., Morelli, B., Henderson, A., Chiang, E., Beck, A., Cashman, S., Wexler, E., McGaughy, K., & Martell, A. (2023). From Field to Bin: The Environmental Impact of U.S. Food Waste Management Pathways (No. EPA/600/R-23/065). U.S. Environmental Protection Agency Office of Research and Development. Link to source: https://www.epa.gov/land-research/field-bin-environmental-impacts-us-food-waste-management-pathways

Kummu, M., De Moel, H., Porkka, M., Siebert, S., Varis, O., & Ward, P. J. (2012). Lost food, wasted resources: Global food supply chain losses and their impacts on freshwater, cropland, and fertiliser use. Science of The Total Environment, 438, 447-489. Link to source: https://doi.org/10.1016/j.scitotenv.2012.08.092

Lipinski, B. (2024). SDG target 12.3 on food loss and waste: 2024 progress report. Champions 12.3. Link to source: https://champions123.org/sites/default/files/2024-09/champions-12-3-2024-progress-report.pdf

Mbow, C., C. Rosenzweig, L.G. Barioni, T.G. Benton, M. Herrero, M. Krishnapillai, E. Liwenga, P. Pradhan, M.G. Rivera-Ferre, T. Sapkota, F.N. Tubiello, Y. Xu, (2019). Food Security. In P.R. Shukla, J. Skea, E. Calvo Buendia, V. Masson-Delmotte, H.-O. Pörtner, D.C. Roberts, P. Zhai, R. Slade, S. Connors, R. van Diemen, M. Ferrat, E. Haughey, S. Luz, S. Neogi, M. Pathak, J. Petzold, J. Portugal Pereira, P. Vyas, E. Huntley, K. Kissick, M. Belkacemi, J. Malley, (Eds.), Climate Change and Land: an IPCC special report on climate change, desertification, land degradation, sustainable land management, food security, and greenhouse gas fluxes in terrestrial ecosystems . Cambridge University Press. Link to source: https://www.ipcc.ch/srccl/chapter/chapter-5/ 

Marston, L. T., Read, Q. D., Brown, S. P., & Muth, M. K. (2021). Reducing water scarcity by reducing food loss and waste. Frontiers in Sustainable Food Systems, 5. Link to source: https://doi.org/10.3389/fsufs.2021.651476

Moraes, N. V., Lermen, F. H., & Echeveste, M. E. S. (2021). A systematic literature review on food waste/loss prevention and minimization methods. Journal of Environmental Management, 286. Link to source: https://doi.org/10.1016/j.jenvman.2021.112268

Nabuurs, G.-J., Mrabet, R., Hatab, A. A., Bustamante, M., Clark, H., Havlík, P., House, J., Mbow, C., Ninan, K. N., Popp, A., Roe, S., Sohngen, B., and Towprayoon, S. (2022). Agriculture, Forestry and Other Land Uses (AFOLU). In P. R. Shukla, J. Skea, R. Slade, A. A. Khourdajie, R. v. Diemen, D. McCollum, M. Pathak, S. Some, P. Vyas, R. Fradera, M. Belkacemi, A. Hasija, G. Lisboa, S. Luz, & J. Malley (Eds.), Climate Change 2022: Mitigation of Climate Change. Contribution of Working Group III to the Sixth Assessment Report of the Intergovernmental Panel on Climate Change (1st ed, pp. 747-860). . Cambridge, UK and New York, NY, USA: Cambridge University Press. Link to source: https://doi.org/10.1017/9781009157926.009 

Neff, R. A., Kanter, R., & Vandevijvere, S. (2015). Reducing food loss and waste while improving the public’s health. Health Affairs, 34(11): 1821-1829. Link to source: https://doi.org/10.1377/hlthaff.2015.0647

Nutrition Connect. (2023). Reducing Waste from Farm to Plate: A Multi-Stakeholder Recipe to Reduce Food Loss and Waste. Global Alliance for Improved Nutrition (GAIN). Link to source: https://nutritionconnect.org/news-events/reducing-food-loss-waste-farm-plate-stakeholder-recipe-compendium

Poore, J., & Nemecek, T. (2018). Reducing food’s environmental impacts through producers and consumers. Science, 360(6392): 987-992. Link to source: https://doi.org/10.1126/science.aaq0216

Porter, S. D., Reay, D. S., Higgins, P., & Bomberg, E. (2016). A half-century of production-phase greenhouse gas emissions from food loss & waste in the global food supply chain. Science of the Total Environment, 571: 721-729. Link to source: https://doi.org/10.1016/j.scitotenv.2016.07.041

Read, Q. D., Brown, S., Cuellar, A. D., Finn, S. M., Gephart, J. A., Marston, L. T., Meyer, E., Weitz, K.A., & Muth, M. K. (2020). Assessing the environmental impacts of halving food loss and waste along the food supply chain. Sci Total Environ, 712. Link to source: https://doi.org/10.1016/j.scitotenv.2019.136255 

Read, Q. D., & Muth, M. K. (2021). Cost-effectiveness of four food waste interventions: Is food waste reduction a “win–win?”. Resources, Conservation and Recycling, 168. Link to source: https://doi.org/10.1016/j.resconrec.2021.105448 

ReFED. (2024). The Methane Impact of Food Loss and Waste in the United States. Link to source: https://refed.org/uploads/refed-methane-report-final.pdf

Reynolds, C., Goucher, L., Quested, T., Bromley, S., Gillick, S., Wells, V. K., Evans, D., Koh, L., Carlsson Kanyama, A., Katzeff, C., Svenfelt, A., & Jackson, P. (2019). Review: Consumption-stage food waste reduction interventions – What works and how to design better interventions. Food Policy, 83: 7-27. Link to source: https://doi.org/10.1016/j.foodpol.2019.01.009 

Rolker, H., Eisler, M., Cardenas, L., Deeney, M., & Takahashi, T. (2022). Food waste interventions in low-and-middle-income countries: A systematic literature review. Resources, Conservation and Recycling, 186. Link to source: https://doi.org/10.1016/j.resconrec.2022.106534 

Searchinger, T., Waite, R., Hanson, C., & Ranganathan, J. (2019). Creating a Sustainable Food Future. World Resources Institute.  https://research.wri.org/sites/default/files/2019-07/WRR_Food_Full_Report_0.pdf

Sheahan, M., & Barrett, C. B. (2017). Review: Food loss and waste in Sub-Saharan Africa. Food Policy, 70: 1-12. Link to source: https://doi.rog/10.1016/j.foodpol.2017.03.012 

Kaza, Silpa, Lisa Yao, Perinaz Bhada-Tata, and Frank Van Woerden (2018). What a Waste 2.0: A Global Snapshot of Solid Waste Management to 2050. Urban Development Series. Washington, DC: World Bank. doi:10.1596/978-1-4648 -1329-0. License: Creative Commons Attribution CC BY 3.0 IGO

Swannell, R., Falconer Hall, M., Tay, R., & Quested, T. (2019). The food waste atlas: An important tool to track food loss and waste and support the creation of a sustainable global food system. Resources, Conservation and Recycling, 146: 534-545. Link to source: https://doi.org/10.1016/j.resconrec.2019.02.006

Thi, N. B. D., Kumar, G., & Lin, C.-Y. (2015). An overview of food waste management in developing countries: Current status and future perspective. Journal of Environmental Management, 157: 220-229. Link to source: https://doi.org/10.1016/j.jenvman.2015.04.022

Tubiello, F. N., Karl, K., Flammini, A., Gütschow, J., Obli-Laryea, G., Conchedda, G., Pan, X., Qi, S. Y., Halldórudóttir Heiðarsdóttir, H., Wanner, N., Quadrelli, R., Rocha Souza, L., Benoit, P., Hayek, M., Sandalow, D., Mencos Contreras, E., Rosenzweig, C., Rosero Moncayo, J., Conforti, P., & Torero, M. (2022). Pre- and post-production processes increasingly dominate greenhouse gas emissions from agri-food systems. Earth System Science Data, 14(4): 1795-1809. Link to source: https://doi.org/10.5194/essd-14-1795-2022

UNEP. (2024). Food Waste Index Report 2024. Think Eat Save: Tracking Progress to Halve Global Food Waste. Link to source: https://wedocs.unep.org/xmlui/handle/20.500.11822/45230

U.S. Food and Drug Administration. (2019). Food Facts: How to Cut Food Waste and Maintain Food Safety. Food and Drug Administration. Link to source: https://www.fda.gov/food/consumers/how-cut-food-waste-and-maintain-food-safety 

WasteMAP | Home. (n.d.). Retrieved October 24, 2024, from Link to source: https://wastemap.earth/

Wilson, N. L. W., Rickard, B. J., Saputo, R., & Ho, S.-T. (2017). Food waste: The role of date labels, package size, and product category. Food Quality and Preference, 55, 35-44. Link to source: https://doi.org/10.1016/j.foodqual.2016.08.004 

World Bank. (2020). Addressing Food Loss and Waste: A Global Problem with Local Solutions. World Bank. Link to source: https://openknowledge.worldbank.org/entities/publication/1564bf5c-ed24-5224-b5d8-93cd62aa3611

WRAP (2023). UK Food System Greenhouse Gas Emissions: Progress towards the Courtauld 2030 target. Link to source: https://www.wrap.ngo/sites/default/files/2024-05/WRAP-MIANZW-Annual-Progress-Summary-report-22-23-Variation-1-2024-04-30.pdf

WRAP (2024). UK Food System Greenhouse Gas Emissions: Progress towards the Courtauld 2030 target. https://www.wrap.ngo/sites/default/files/2024-12/WRAP-Courtauld-2030-GHG-2324.pdf 

WWF-UK. (2021). Driven to waste: The Global Impact of Food Loss and Waste on Farms. Retrieved from Link to source: https://files.worldwildlife.org/wwfcmsprod/files/Publication/file/5p58sxloyr_technical_report_wwf_farm_stage_food_loss_and_waste.pdf 

WWF-WRAP. (2020). Halving Food Loss and Waste in the EU by 2030: the major steps needed to accelerate progress. Retrieved from Link to source: https://www.wrap.ngo/resources/report/halving-food-loss-and-waste-eu-2030-major-steps-needed-accelerate-progress 

Xue, L., Liu, G., Parfitt, J., Liu, X., Herpen, E. V., O’Connor, C., Östergren, K., & Cheng, S. 2017. Missing food, missing data? A critical review of global food losses and food waste data. Env Sci Technol. 51, 6618-6633. Link to source: https://doi.org/10.1021/acs.est.7b00401 

Ziervogel, G., & Ericksen, P. J. (2010). Adapting to climate change to sustain food security. WIREs Climate Change, 1(4), 525-540. Link to source: https://doi.org/10.1002/wcc.56 

Zhu, J., Luo, Z., Sun, T., Li, W., Zhou, W., Wang, X., Fei, X., Tong, H., & Yin, K. (2023). Cradle-to-grave emissions from food loss and waste represent half of total greenhouse gas emissions from food systems. Nature Food, 4(3), 247-256. Link to source: https://doi.org/10.1038/s43016-023-00710-3

Credits

Lead Fellows

  • Erika Luna

  • Aishwarya Venkat, Ph.D.

Contributors

  • Ruthie Burrows, Ph.D.

  • Emily Cassidy, Ph.D.

  • James Gerber, Ph.D.

  • Yusuf Jameel, Ph.D.

  • Daniel Jasper

  • Alex Sweeney

  • Eric Toensmeier

  • Paul C. West, Ph.D.

Internal Reviewers

  • Aiyana Bodi

  • Hannah Henkin

  • Megan Matthews, Ph.D.

  • Heather McDiarmid, Ph.D.

  • Ted Otte

  • Christina Swanson, Ph.D.

  • Paul C. West, Ph.D.

Effectiveness

Our analysis estimates that reducing FLW reduces emissions 2.82 t CO₂‑eq (100-yr basis) for every metric ton of food saved (Table 1). This estimate is based on selected country and global assessments from nongovernmental organizations (NGOs), public agencies, and development banks (ReFED, 2024; World Bank, 2020; WRAP, 2024). All studies included in this estimation reported a reduction in both volumes of FLW and GHG emissions. However, it is important to recognize that the range of embodied emissions varies widely across foods (Poore and Nemecek, 2018). For example, reducing meat waste can be more effective than reducing fruit waste because the embodied emissions are much higher.

Effectiveness is only reported on a 100-yr time frame here because our data sources did not include enough information to separate out the contribution of different GHGs and calculate the effectiveness on a 20-yr time frame.

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Table 1. Effectiveness at reducing emissions.

Unit: t CO₂‑eq /t reduced FLW, 100-yr basis

25th percentile 2.75
mean 3.11
median (50th percentile) 2.82
75th percentile 3.30
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Cost

The net cost of baseline FLW is US$932.55/t waste, based on values from the Food and Agriculture Organization of the United Nations (FAO, 2014) and Hegensholt et al. (2018). The median net cost of implementing strategies and practices that reduce FLW is US$385.50/t waste reduced, based on values from ReFED (2024) and Hanson and Mitchell (2017). These costs include, but are not limited to, improvements to inventory tracking, storage, and diversion to food banks. Therefore, the net cost of the solution compared to baseline is a total savings of US$547.05/t waste reduced. 

Therefore, reducing emissions for FLW is cost-effective, saving US$193.99/t avoided CO2 -eq on a 100-yr basis (Table 2).

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Table 2. Net cost per unit climate impact.

Unit: US$/t CO₂‑eq , 2023

Median (100-yr basis) -193.99
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Learning Curve

Learning curve data are not yet available for this solution.

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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as emergency brake, gradual, or delayed.

Reduce Food Loss and Waste is an EMERGENCY BRAKE climate solution. It has the potential to deliver a more rapid impact than nominal and delayed solutions. Because emergency brake solutions can deliver their climate benefits quickly, they can help accelerate our efforts to address dangerous levels of climate change. For this reason, they are a high priority.

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Caveats

Reducing FLW through consumer behavior, supply chain efficiencies, or other means can lead to lower food prices, creating a rebound effect that leads to increased consumption and GHG emissions (Hegwood et al., 2023). This rebound effect could offset around 53–71% of the mitigation benefits (Hegwood et al., 2023). Population and economic growth also increase FLW. The question remains however, who should bear the cost of implementing FLW solutions. A combination of value chain investments by governments and waste taxes for consumers may be required for optimal FLW reduction (Gatto, 2023; Hegwood, 2023; The World Bank, 2020). 

Strategies for managing post-consumer waste through composting and landfills are captured in other Project Drawdown solutions (see Improve Landfill Management, Increase Composting, and Deploy Methane Digesters solutions).

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Current Adoption

Due to a lack of data we were not able to quantify current adoption for this solution.

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Adoption Trend

Data on adoption trends were not available.

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Adoption Ceiling

We assumed an adoption ceiling of 1.75 Gt of FLW reduction in 2023, which reflects a 100% reduction in FLW (Table 3). While reducing FLW by 100% is unrealistic because some losses and waste are inevitable (e.g., trimmings, fruit pits and peels) and some surplus food is needed to ensure a stable food supply (HLPE, 2014), we kept that simple assumption because there wasn’t sufficient information on the amount of inevitable waste, and it is consistent with other research used in this assessment.

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Table 3. Adoption ceiling.

Unit: t FLW reduced/yr

Median 1,750,000,000
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Achievable Adoption

Studies consider that halving the reduction in FLW by 2050 is extremely ambitious and would require “breakthrough technologies,” whereas a 25% reduction is classified as highly ambitious, and a 10% reduction is more realistic based on coordinated efforts (Searchinger, 2019; Springmann et al., 2018). With our estimation of 1.75 Gt of FLW per year, a 25% reduction equals 0.48 Gt, while a 50% reduction would represent 0.95 Gt of reduced FLW.

It is important to acknowledge that, 10 years after the 50% reduction target was set in the Sustainable Development Goals (SDGs, Goal 12.3), the world has not made sufficient progress. The challenge has therefore become larger as the amounts of FLW keep increasing at a rate of 2.2%/yr (Gatto & Chepeliev, 2023; Hegnsholt, et al. 2018; Porter et al., 2016).

As a result of these outcomes, we have selected a 25% reduction in FLW as our Achievable – Low and 50% as our Achievable – High. Reductions in FLW are 437.5, 875, and 1,750 mt FLW/year for Achievable – Low, Achievable – High, and Adoption Ceiling, respectively (Table 4).

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Table 4: Adoption levels.

Unit: t FLW reduced/yr

Current adoption (baseline) Not determined
Achievable – Low (25% of total FLW) 437,500,000
Achievable – High (50% of total FLW) 875,000,000
Adoption ceiling (100% of total FLW) 1,750,000,000
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An Achievable – Low (25% FLW reduction) could represent 1.23 Gt CO₂‑eq/yr (100-yr basis) of reduced emissions, whereas an Achievable – High (50% FLW reduction) could represent up to 2.47 Gt CO₂‑eq/yr. The adoption potential (100% FLW reduction) would result in 4.94 Gt CO₂‑eq/yr (Table 5). We are only able to report emissions outcomes on a 100-yr basis here because our data sources generally did not separate out the emissions from shorter-lived GHGs such as from methane or report emissions on a 20-yr basis. 

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Table 5. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current adoption (1.5% of total FLW) Not determined
Achievable – Low (25% of total FLW) 1.23
Achievable – High (50% of total FLW) 2.47
Adoption ceiling (100% of total FLW) 4.94
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We also compiled studies that have modeled the climate impacts of different FLW reduction scenarios, from 10% to 75%. For an achievable 25% reduction, Scheringer (2019) estimated a climate impact of 1.6 Gt CO₂‑eq/yr. Studies that modeled the climate impact of a 50% reduction by 2050 estimated between 0.5 Gt CO₂‑eq/yr (excluding emissions from agricultural production and land use change; Roe at al., 2021) to 3.1–4.5 Gt CO₂‑eq/yr (including emissions from agricultural production and land use change; Roe at al., 2021; Searchinger et al., 2019).

Multiple studies stated that climate impacts from FLW reduction would be greater when combined with the implementation of dietary changes (see the Improve Diets solution; Almaraz et al., 2023; Babiker et al.; 2022; Roe et al., 2021; Springmann et al., 2018; Zhu et al., 2023).

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Additional Benefits

Extreme Weather Events

Households and communities can strengthen adaptation to climate change by improving food storage, which helps reduce food loss (Ziervogel & Ericksen, 2010). Better food storage infrastructure improves food security from extreme weather events such as drought or floods which make it more difficult to grow food and can disrupt food distribution (Mbow et al., 2020). 

Income and Work

FLW accounts for a loss of about US$1 trillion annually (World Bank, 2020). In the United States, a four-person household spends about US$2,913 on food that is wasted (Kenny, 2025). These household-level savings are particularly important for low-income families because they commonly spend a higher proportion of their income on food (Davidenko & Sweitzer, 2024). Reducing FLW can improve economic efficiency (Jaglo et al., 2021). In fact, a report by Champions 12.3 found efforts to reduce food waste produced positive returns on investments in cities, businesses, and households in the United Kingdom (Hanson & Mitchell, 2017). FLW in low- and middle-income mostly occurs during the pre-consumer stages, such as during storage, processing, and transport (World Bank, 2018). Preventive measures to reduce these losses have been linked to improved incomes and profits (Rolker et al., 2022). 

Food Security

Reducing FLW increases the amount of available food, thereby improving food security without requiring increased production (Neff et al., 2015). The World Resources Institute estimated that halving the rate of FLW could reduce the projected global need for food approximately 20% by 2050 (Searchinger et al., 2019). In the United States, about 30–40% of food is wasted (U.S. Food and Drug Administration [U.S. FDA], 2019) with this uneaten food accounting for enough calories to feed more than 150 million people annually (Jaglo et al., 2021). These studies demonstrate that reducing FLW can simultaneously decrease the demand for food production while improving food security.

Health

Policies that reduce food waste at the consumer level, such as improved food packaging and clearer information on shelf life and date labels, can reduce the number of foodborne illnesses (Neff et al., 2015; U.S. FDA, 2019). Additionally, efforts to improve food storage and food handling can further reduce illnesses and improve working conditions for food-supply-chain workers (Neff et al., 2015). Reducing FLW can lower air pollution from food production, processing, and transportation, and from disposal of wasted food (Nutrition Connect, 2023). Gatto and Chepeliev (2024) found that reducing FLW can improve air quality (primarily through reductions in carbon monoxide, ammonia, nitrogen oxides, and particulate matter), which lowers premature mortality from respiratory infections. These benefits were primarily observed in China, India, and Indonesia, where high FLW-embedded air pollution is prevalent across all stages of the food supply chain (Gatto & Chepeliev, 2024).

Land Resources

For a description of the land resources benefits, please refer to the “water resources” subsection. 

Water Resources

Reducing FLW can conserve resources and improve biodiversity (Cattaneo, Federighi, & Vaz, 2021). A reduction in FLW reflects improvements in resource efficiency of freshwater, synthetic fertilizers, and cropland used for agriculture (Kummu et al., 2012). Reducing the strain on freshwater resources is particularly relevant in water-scarce areas such as North Africa and West-Central Asia (Kummu et al., 2012). In the United States, halving the amount of FLW could reduce approximately 290,000 metric tons of nitrogen from fertilizers, thereby reducing runoff, improving water quality, and decreasing algal blooms (Jaglo et al., 2021).

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Risks

Some FLW reduction strategies have trade-offs for emission reductions (de Gorter et al., 2021; Cattaneo, 2021). For example, improved cold storage and packaging are important interventions for reducing food loss, yet they require additional energy and refrigerants, which can increase GHG emissions (Babiker, 2017; FAO, 2019).

Interventions to address FLW also risk ignoring economic factors such as price transmission mechanisms and cascading effects, both upstream and downstream in the supply chain. The results of a FLW reduction policy or program depend greatly on the commodity, initial FLW rates, and market integration (Cattaneo, 2021; de Gorter, 2021).

The production site is a critical loss point, and farm incomes, scale of operations, and expected returns to investment affect loss reduction interventions (Anriquez, 2021; Fabi, 2021; Sheahan and Barrett, 2017).

On the consumer side, there is a risk of a rebound effect; i.e., avoiding FLW can lower food prices, leading to increased consumption and net increase in GHG emissions (Hegwood et al., 2023). Available evidence is highly contextual and often difficult to scale, so relevant dynamics must be studied with care (Goossens, 2019).

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Interactions with Other Solutions

Competing

Food waste is used as raw material for methane digestors and composting. Reducing FLW may reduce the impact of those solutions as a result of decreased feedstock availability.

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Dashboard

Solution Basics

t reduced FLW

t CO₂-eq (100-yr)/unit
02.752.82
units/yr
Current Not Determined 04.375×10⁸8.75×10⁸
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current Not Determined 1.232.47
US$ per t CO₂-eq
Emergency Brake

CO₂ , CH₄ , N₂O

Action Word
Reduce
Solution Title
Food Loss & Waste
Classification
Highly Recommended
Lawmakers and Policymakers
  • Ensure public procurement uses strategies to reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Use financial incentives and regulations to promote efficient growing practices, harvesting methods, and storage technologies.
  • Utilize financial instruments such as taxes, subsidies, or exemptions to support infrastructure, technology, and enforcement.
  • Implement bans on food waste in landfills.
  • Standardize food date labels.
  • Mandate FLW reporting and reduction targets for major food businesses.
  • Prioritize policies that divert FLW toward human consumption first, then prioritize animal feed or compost.
  • Fund research to improve monitoring technologies, food storage, and resilient crop varieties.
  • Invest or expand extension services to work with major food businesses to reduce FLW.
  • Invest in and improve supportive infrastructure including electricity, public storage facilities, and roads to facilitate compost supply chains.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Practitioners
  • Ensure operations reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Set ambitious targets to reduce FLW, reevaluate them regularly, and use thorough measurements that capture FLW, associated GHG emissions, and financial data.
  • Take advantage of extension services and financial incentives such as tax rebates and subsidies that promote FLW reduction strategies.
  • Work with policymakers, peers, and industry leaders to standardize date labeling.
  • Promote cosmetically imperfect food through marketing, discounts, or offtake agreements.
  • Utilize behavior change mechanisms such as signage saying “eat what you take,” offer smaller portion sizes, use smaller plates for servings, and visibly post information on the impact of FLW and best practices for prevention.
  • Engage with front-line workers to identify and remedy FLW.
  • Institute warehouse receipt systems and tracking techniques.
  • Use tested storage devices and facilities such as hermetic bags and metal silos.
  • Utilize Integrated Pest Management (IPM) during both pre- and post-harvest stages.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Business Leaders
  • Ensure procurement uses strategies to reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Set ambitious targets to reduce FLW, reevaluate them regularly, and use thorough measurements that capture FLW, associated GHG emissions, and financial data.
  • Utilize or work with companies that utilize efficient growing practices, harvesting methods, and storage technologies that reduce FLW.
  • Enter into offtake agreements for diverted food initiatives.
  • Promote cosmetically imperfect food through marketing, discounts, or offtake agreements.
  • Work with policymakers and industry peers to standardize date labeling and advocate for bans on food waste in landfills.
  • Appoint a senior executive responsible for FLW goals and ensure they have the resources and authority for effective implementation.
  • Utilize behavior change mechanisms such as signage saying, “eat what you take,” offer smaller portion sizes, use smaller plates for servings, and visibly post information on the impact of FLW and best practices for prevention.
  • Engage with front-line workers to identify and remedy FLW.
  • Institute warehouse receipt systems and tracking techniques.
  • Fund research or startups that aim to improve monitoring technologies, food storage, packaging materials, stocking practices, and resilient crop varieties.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Nonprofit Leaders
  • Ensure procurement uses strategies to reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Advocate for bans on food waste in landfills.
  • Work with policymakers and industry leaders to standardize date labeling.
  • Assist food and agricultural companies with utilizing efficient growing practices, harvesting methods, and storage technologies that reduce FLW.
  • Advocate for financial instruments such as taxes, subsidies, or exemptions to support infrastructure, technology, and enforcement.
  • Use cosmetically imperfect and diverted food for food banks.
  • Assist companies in tracking and reporting FLW, monitoring goals, and offering input for improvement.
  • Help transfer capacity, knowledge, and infrastructure to support FLW management in low- and middle-income communities.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Investors
  • Ensure portfolio companies and company procurement use strategies to reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Require portfolio companies to measure and report on FLW emissions.
  • Fund startups which aim to improve monitoring technologies, food storage, packaging materials, stocking practices, and resilient crop varieties.
  • Offer financial services, notably rural financial market development, including low-interest loans, micro-financing, and grants to support FLW initiatives.
  • Create, support, or join education campaigns and/or public-private partnerships, such as the Food Waste Funder Circle, that facilitate stakeholder discussions.

Further information:

Philanthropists and International Aid Agencies
  • Ensure procurement uses strategies to reduce FLW at all stages of the supply chain; consider using the Food Loss and Waste Protocol.
  • Advocate for bans on food waste in landfills.
  • Work with policymakers and industry leaders to standardize date labeling.
  • Assist food and agricultural companies with utilizing efficient growing practices, harvesting methods, and storage technologies that reduce FLW.
  • Advocate for financial instruments such as taxes, subsidies, or exemptions to support infrastructure, technology, and enforcement.
  • Use cosmetically imperfect and diverted food for food banks.
  • Assist companies in tracking and reporting FLW, monitoring goals, and offering input for improvement.
  • Help transfer capacity, knowledge, and infrastructure to support FLW management in low- and middle-income communities.
  • Fund startups that aim to improve monitoring technologies, food storage, packaging materials, stocking practices, and resilient crop varieties.
  • Offer financial services, especially for rural financial market development, including low-interest loans, micro-financing, and grants to support FLW initiatives.
  • Create, support, or join education campaigns and/or public-private partnerships, such as the Food Waste Funder Circle, that facilitate stakeholder discussions.

Further information:

Thought Leaders
  • Adopt behaviors to reduce FLW including portion control, “eating what you take,” and reducing meat consumption.
  • Advocate for bans on food waste in landfills.
  • Assist food and agricultural companies with utilizing efficient growing practices, harvesting methods, and storage technologies that reduce FLW.
  • Work with policymakers and industry leaders to standardize date labeling.
  • Advocate for financial instruments such as taxes, subsidies, or exemptions to support infrastructure, technology, and enforcement.
  • Assist companies or independent efforts in tracking and reporting FLW data and emissions.
  • Help transfer capacity, knowledge, and infrastructure to support FLW management in low- and middle-income communities.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Technologists and Researchers
  • Research and develop more efficient growing and harvesting practices.
  • Develop new crop varieties to increase land productivity, shelf life, durability during transportation, and resistance to contamination.
  • Improve the efficiency of cold chains for transportation and storage.
  • Design software that can optimize the harvesting, storage, transportation, stocking, and shelf life of produce.
  • Improve data collection on FLW, associated GHG emissions, and financial data across the supply chain.
  • Develop new non-plastic, biodegradable, low-carbon packaging materials.
  • Improve storage devices and facilities such as hermetic bags and metal silos.
  • Research technologies, practices, or nonharmful substances to prolong the lifespan of food.

Further information:

Communities, Households, and Individuals
  • Adopt behaviors to reduce FLW including portion control, “eating what you take,” and reducing meat consumption.
  • Donate food that won’t be used or, if that’s not possible, use the food for animals or compost.
  • Advocate for bans on food waste in landfills.
  • Advocate for financial instruments such as taxes, subsidies, or exemptions to support infrastructure, technology, and enforcement.
  • Demand transparency around FLW from public and private organizations.
  • Educate yourself and those around you about the impacts and solutions.
  • Create, support, or join education campaigns and/or public-private partnerships that facilitate stakeholder discussions.

Further information:

Sources
Evidence Base

A large volume of scientific research exists regarding reducing emissions of FLW effectively. The IPCC Sixth Assessment Report (AR6) estimates the mitigation potential of FLW reduction (through multiple reduction strategies) to be 2.1 Gt CO₂‑eq/yr (with a range of 0.1–5.8 Gt CO₂‑eq/yr ) (Nabuurs et al., 2022). This accounts for savings along the whole value chain.

Following the 2011 Food and Agriculture Organization (FAO) of the United Nations (UN) report – which estimated that around one-third (1.3 Gt) of food is lost and wasted worldwide per year – global coordination has prioritized the measurement of the FLW problem. This statistic, provided by the FAO, has served as a baseline for multiple FLW reduction strategies. However, more recent studies suggest that the percentage of FLW may be closer to 40% (WWF, 2021). The median of the studies included in our analysis is 1.75 Gt of FLW per year (Gatto & Chepeliev, 2024; FAO, 2024; Guo et al., 2020; Porter et al., 2016; UNEP, 2024; WWF, 2021; Zhu et al., 2023), with an annual increasing trend of 2.2%.

Only one study included in our analysis calculated food embodied emissions from all stages of the supply chain, while the rest focused on the primary production stages. Zhu et al. (2023) estimated 6.5 Gt CO₂‑eq/yr arising from the supply chain side, representing 35% of total food system emissions.

When referring to food types, meat and animal products were estimated to emit 3.5 Gt CO₂‑eq/yr compared to 0.12 Gt CO₂‑eq/yr from fruits and vegetables (Zhu et al., 2023). Although meat is emissions-intensive, fruits and vegetables are the most wasted types of food by volume, making up 37% of total FLW by mass (Chen et al., 2020). The consumer stage is associated with the highest share of global emissions at 36% of total supply-embodied emissions from FLW, compared to 10.9% and 11.5% at the retail and wholesale levels, respectively (Zhu et al., 2023). 

While efforts to measure the FLW problem are invaluable, critical gaps exist regarding evidence on the effectiveness of different reduction strategies across supply chain stages ( Cattaneo, 2021; Goossens, 2019; Karl et al., 2025). To facilitate impact assessments and cost-effectiveness, standardized metrics are required to report actual quantities of FLW reduced as well as resulting GHG emissions savings (Food Loss and Waste Protocol, 2024).

The results presented in this document summarize findings across 22 studies. These studies are made up of eight academic reviews and original studies, eight reports from NGOs, and six reports from public and multilateral organizations. This reflects current evidence from five countries, primarily the United States and the United Kingdom. We recognize this limited geographic scope creates bias, and hope this work inspires research for meta-analyses and data sharing on this topic in underrepresented regions and stages of the supply chain.

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Manage Oil & Gas Methane

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Summary

Oil and gas methane management is the process of reducing methane emissions from oil and gas (O&G) supply chains. These supply chains release methane when pipes and other system parts leak or methane is intentionally vented for operation and safety reasons. We define the Manage Oil & Gas Methane solution as adopting approaches to reduce methane emissions, including fixing leaks in components, upgrading control equipment, changing procedures, and destroying methane by burning methane as a fuel or in flares.

Food security,Health
Air quality
Description for Social and Search
We define the Manage Oil & Gas Methane solution as adopting approaches to reduce methane emissions, including fixing leaks in components, upgrading control equipment, changing procedures, and destroying methane by burning methane as a fuel or in flares.
Overview

Methane can be unintentionally released due to imperfections and faults along the supply chain or intentionally released as part of operations and maintenance. Atmospheric methane has a GWP of 81 over a 20-yr time basis and a GWP of 28 over a 100-yr time basis (IPCC, 2023). This means methane is 81 times more effective at trapping heat than CO₂.  Because methane is a short-lived climate pollutant that has a much stronger warming effect than CO₂ over a given time period, abating methane will have a relatively large near-term impact on slowing global climate change (IEA, 2023b).

The first step to reduce methane releases from O&G production is to identify where releases occur along the supply chain. Many occur during O&G extraction as methane is either intentionally vented or unintentionally emitted. The International Energy Agency (IEA, 2024) estimated more than 60% of global energy-related methane emissions originated from the O&G sector in 2023, with the remaining emissions mostly coming from coal use and some bioenergy (Figure 1). The United Nations Environment Programme (UNEP) has formed a transparency and accountability initiative whose members are responsible for 42% of global O&G production. It reported that activities involved in exploration and processing of O&G accounted for 83% of total reported O&G emissions from 2020 to 2023, with production processes being responsible for 90% of those emissions (UNEP 2024). Alvarez et al. (2018) found that in the United States, more than 58% of O&G methane emissions came from production and about 20% came from extraction in 2015. 

Figure 1. Methane emissions (kt) from energy sources (IEA, 2025).

Source: International Energy Agency. (2025). Methane tracker: Data tools. https://www.iea.org/data-and-statistics/data-tools/methane-tracker 

O&G producers can reduce their methane emissions by preventing its release or by converting it to CO₂ through combustion. Strategies for reducing O&G methane emissions can be put into two broad categories (Climate & Clean Air Coalition [CCAC], 2021):

Device conversion, replacement, and installation is the practice of fixing leaks in pipes, valves, compressors, pumps, and other equipment. This can include converting natural gas–powered devices to electric, driving compressors/pneumatics with air instead of natural gas, or replacing emitting components with non-emitting ones (Pembina Institute, 2024).

Changes to operations and maintenance practices seek to reduce the intentional venting of methane. They include eliminating the need for blow-down (releasing gases during the maintenance or operation of pipe infrastructure), reducing venting, and capturing methane before it is released into the atmosphere, then using it as fuel for product refining or burning it to convert it into CO₂.

Leak detection and repair (LDAR) is the practice of regularly monitoring for methane leaks and modifying or replacing leaking equipment. 

Alvarez, R., Zavala-Araiza, D., Lyon, D. R., Allen, D. T., Barkley, Z. B., Brandt, A. R., Davis, K. J., Herndon, S. C., Jacob, D. J., Karion, A., Kort, E. A., Lamb, B. K., Lauvaux, T., Maasakkers, J. D., Marchese, A. J., Omara, M., Pacala, S. W., Peischl, J., Robinson, A. L., Shepson, P. B., Sweeney, C., Townsend-Small, A., Wofsy, S. C., & Hamburg, S. P. (2018). Assessment of methane emissions from the U.S. oil and gas supply chain. Science, 361(6398), 186-188. Link to source: https://doi.org/10.1126/science.aar7204 

Anejionu, O. C., Whyatt, J. D., Blackburn, G. A., & Price, C. S. (2015). Contributions of gas flaring to a global air pollution hotspot: spatial and temporal variations, impacts and alleviation. Atmospheric Environment, 118, 184-193. Link to source: https://doi.org/10.1016/j.atmosenv.2015.08.006 

Beck, C., Rashidbeigi, S., Roelofsen, O., & Speelman, E. (2020). The future is now: how oil and gas companies can decarbonize. McKinsey & Company. Link to source: https://www.mckinsey.com/industries/oil-and-gas/our-insights/the-future-is-now-how-oil-and-gas-companies-can-decarbonize 

Carbon Limits. (2014). Quantifying cost-effectiveness of systematic leak detection and repair program using infrared cameras. Link to source: https://www.catf.us/resource/quantifying-cost-effectiveness-ldar/ 

Clean Air Task Force. (2022). Fossil fumes (2022 update): A public health analysis of toxic air pollution from the oil and gas industry. Link to source: https://www.catf.us/resource/fossil-fumes-public-health-analysis/ 

Climate & Clean Air Coalition. (2021). Global methane assessment: Summary for decision makers. Link to source: https://www.ccacoalition.org/resources/global-methane-assessment-summary-decision-makers 

Climate & Clean Air Coalition. (n.d.). Methane. Retrieved July 19, 2024. Link to source: https://www.ccacoalition.org/short-lived-climate-pollutants/methane#:~:text=While%20methane%20does%20not%20cause,rise%20in%20tropospheric%20ozone%20levels. 

Climateworks Foundation. (2024). Reducing methane emissions on a global scale. Link to source: https://climateworks.org/blog/reducing-methane-emissions-on-a-global-scale/ 

Conrad, B. M., Tyner, D. R., Li, H. Z., Xie, D. & Johnson, M. R. (2023). A measurement-based upstream oil and gas methane inventory for Alberta, Canada reveals higher emissions and different sources than official estimates. Earth & Environment. Link to source: https://doi.org/10.1038/s43247-023-01081-0 

DeFabrizio, S., Glazener, W., Hart, C., Henderson, K., Kar, J., Katz, J., Pratt, M. P., Rogers, M., Ulanov, A., & Tryggestad, C. (2021). Curbing methane emissions: How five industries can counter a major climate threat. McKinsey Sustainability. Link to source: https://www.mckinsey.com/~/media/mckinsey/business%20functions/sustainability/our%20insights/curbing%20methane%20emissions%20how%20five%20industries%20can%20counter%20a%20major%20climate%20threat/curbing-methane-emissions-how-five-industries-can-counter-a-major-climate-threat-v4.pdf 

Dunsky. (2023, July 21). Canada’s methane abatement opportunity. Link to source: https://dunsky.com/project/methane-abatement-opportunities-in-the-oil-gas-extraction-sector/ 

Fawole, O. G., Cai, X. M., & MacKenzie, A. R. (2016). Gas flaring and resultant air pollution: A review focusing on black carbon. Environmental pollution, 216, 182-197. Link to source: https://doi.org/10.1016/j.envpol.2016.05.075 

Fiore, A. M., Jacob, D. J., & Field, B. D. (2002). Linking ozone pollution and climate change: The case for controlling methane. Geophysical Research Letters, 29(19), 182-197. Link to source: https://doi.org/10.1029/2002GL015601 

Giwa, S. O., Nwaokocha, C. N., Kuye, S. I., & Adama, K. O. (2019). Gas flaring attendant impacts of criteria and particulate pollutants: A case of Niger Delta region of Nigeria. Journal of King Saud University-Engineering Sciences, 31(3), 209-217. Link to source: https://doi.org/10.1016/j.jksues.2017.04.003 

Global Energy Monitor (2024). Global Methane Emitters Tracker [Data set, September 2024 release]. Retrieved April 18, 2025 from Link to source: https://globalenergymonitor.org/projects/global-methane-emitters-tracker/ 

Global Methane Initiative (2019). GMI methane data EPA [Data set]. Link to source: https://www.globalmethane.org/methane-emissions-data.aspx 

Global Methane Initiative (2024). 2023 Accomplishments in methane mitigation, recovery, and use through U.S.-supported international efforts. Link to source: https://www.epa.gov/gmi/us-government-global-methane-initiative-accomplishments 

Global Methane Pledge. (n.d.). Global methane pledge. Retrieved August 16, 2024 from Link to source: https://www.globalmethanepledge.org/ 

Guarin, J. R., Jägermeyr, J., Ainsworth, E. A., Oliveira, F. A., Asseng, S., Boote, K., ... & Sharps, K. (2024). Modeling the effects of tropospheric ozone on the growth and yield of global staple crops with DSSAT v4. 8.0. Geoscientific Model Development, 17(7), 2547-2567. Link to source: https://doi.org/10.5194/gmd-17-2547-2024 

Hong, C., Mueller, N. D., Burney, J. A., Zhang, Y., AghaKouchak, A., Moore, F. C., Qin, Y., Tong, D., & Davis, S. J. (2020). Impacts of ozone and climate change on yields of perennial crops in California. Nature Food, 1(3), 166-172. Link to source: https://doi.org/10.1038/s43016-020-0043-8 

ICF International. (2016). Economic analysis of methane emission reduction potential from natural gas systems. Link to source: https://onefuture.us/wp-content/uploads/2018/05/ONE-Future-MAC-Final-6-1.pdf 

Intergovernmental Panel on Climate Change (IPCC). (2023). In: Climate change 2023: Synthesis report. Contribution of working groups I, II and III to the sixth assessment report of the intergovernmental panel on climate change [core writing team, H. Lee and J. Romero (eds.)]. IPCC, Geneva, Switzerland, pp. 1-34, doi: 10.59327/IPCC/AR6-9789291691647.001 Link to source: https://www.ipcc.ch/report/ar6/syr/ 

International Energy Agency. (2021). Global methane tracker 2021: Methane abatement and regulation. Link to source: https://www.iea.org/reports/methane-tracker-2021/methane-abatement-and-regulation 

International Energy Agency. (2023a). Financing reductions in oil and gas methane emissions. Link to source: https://www.iea.org/reports/financing-reductions-in-oil-and-gas-methane-emissions 

International Energy Agency. (2023b). Net zero roadmap: A global pathway to keep the 1.5℃ goal in reach - 2023 update. Link to source: https://www.iea.org/reports/net-zero-roadmap-a-global-pathway-to-keep-the-15-0c-goal-in-reach 

International Energy Agency. (2023c). The imperative of cutting methane from fossil fuels. Link to source: https://www.iea.org/reports/the-imperative-of-cutting-methane-from-fossil-fuels 

International Energy Agency. (2023d). World energy outlook 2023. Link to source: https://www.iea.org/reports/world-energy-outlook-2023 

International Energy Agency. (2025). Methane tracker: Data tools. Link to source: https://www.iea.org/data-and-statistics/data-tools/methane-tracker 

Ismail, O. S., & Umukoro, G. E. (2012). Global impact of gas flaring. Energy and Power Engineering, 4(4), 290-302. Link to source: http://dx.doi.org/10.4236/epe.2012.44039 

Johnson, M. R., & Coderre, A. R. (2012). Opportunities for CO2 equivalent emissions reductions via flare and vent mitigation: A case study for Alberta, Canada. International Journal of Greenhouse Gas Control, 8, 121-131. Link to source: https://doi.org/10.1016/j.ijggc.2012.02.004 

Laan, T., Do, N., Haig, S., Urazova, I., Posada, E., & Wang, H. (2024). Public financial support for renewable power generation and integration in the G20 countries. International Institute for Sustainable Development. Link to source: https://www.iisd.org/system/files/2024-09/renewable-energy-support-g20.pdf 

Malley, C. S., Borgford-Parnell, N. Haeussling, S., Howard, L. C., Lefèvre E. N., & Kuylenstierna J. C. I. (2023). A roadmap to achieve the global methane pledge. Environmental Research: Climate, 2(1). Link to source: https://doi.org/10.1088/2752-5295/acb4b4 

Mar, K. A., Unger, C., Walderdorff, L., & Butler, T. (2022). Beyond CO2 equivalence: The impacts of methane on climate, ecosystems, and health. Environmental Science & Policy, 134, 127-136. Link to source: https://doi.org/10.1016/j.envsci.2022.03.027 

Marks, L. (2022). The abatement cost of methane emissions from natural gas production. Journal of the Association of Environmental and Resource Economists, 9(2). Link to source: https://doi.org/10.1086/716700 

Methane Guiding Principles Partnership. (n.d.). Reducing methane emissions on a global scale. Retrieved August 16, 2024 from Link to source: https://methaneguidingprinciples.org/ 

MethaneSAT. (2024). Solving a crucial climate challenge. Retrieved September 2, 2024 Link to source: https://www.methanesat.org/satellite/ 

Michanowicz, D. R., Lebel, E. D., Domen, J. K., Hill, L. A. L., Jaeger, J. M., Schiff, J. E., Krieger, E. M., Banan, Z., Goldman, J. S. W., Nordgaard, C. L., & Shonkoff, S. B.C. (2021). Methane and health-damaging air pollutants from the oil and gas sector: Bridging 10 years of scientific understanding. PSE Healthy Energy. Link to source: https://www.psehealthyenergy.org/work/methane-and-health-damaging-air-pollutants-from-oil-and-gas/ 

Mills, G., Sharps, K., Simpson, D., Pleijel, H., Frei, M., Burkey, K., Emberson, L., Cuddling, J., Broberg, M., Feng, Z., Kobayashi, K. & Agrawal, M. (2018). Closing the global ozone yield gap: Quantification and cobenefits for multistress tolerance. Global Change Biology, 24(10), 4869-4893. Link to source: https://doi.org/10.1111/gcb.14381 

Moore, C. W., Zielinska, B., Pétron, G., & Jackson, R. B. (2014). Air impacts of increased natural gas acquisition, processing, and use: A critical review. Environmental Science & Technology, 48(15), 8349–8359. Link to source: https://doi.org/10.1021/es4053472

Motte, J., Alvarenga, R. A., Thybaut, J. W., & Dewulf, J. (2021). Quantification of the global and regional impacts of gas flaring on human health via spatial differentiation. Environmental Pollution, 291, 118213. Link to source: https://doi.org/10.1016/j.envpol.2021.118213 

National Atmospheric and Ocean Agency (2024). Carbon cycle greenhouse gases in CH4. Retrieved July 19, 2024. Link to source: https://gml.noaa.gov/ccgg/trends_ch4/

Ocko, I. B., Sun, T., Shindell, D., Oppenheimer, M. Hristov, A. N., Pacala, S. W., Mauzerall, D. L., Xu, Y. & Hamburg, S. P. (2021). Acting rapidly to deploy readily available methane mitigation measures by sector can immediately slow global warming. Environmental Research, 16(5). Link to source: https://doi.org/10.1088/1748-9326/abf9c8 

Odjugo, P. A. O. & Osemwenkhae, E. J. (2009). Natural gas flaring affects microclimate and reduces maize (Zea mays) yield.. International Journal of Agriculture and Biology, 11(4), 408-412. Link to source: https://www.cabidigitallibrary.org/doi/full/10.5555/20093194660

Oil and Gas Climate Initiative. (2023). Building towards net zero. Link to source: https://www.ogci.com/progress-report/building-towards-net-zero 

Olczak, M., Piebalgs, A., & Balcombe, P. (2023). A global review of methane policies reveals that only 13% of emissions are covered with unclear effectiveness. One Earth, 6(5), 519–535. Link to source: https://doi.org/10.1016/j.oneear.2023.04.009

Pembina Institute. (2024). Comments on environment and climate change Canada’s (ECCC) regulations amending the regulations respecting reduction in the release of methane and certain volatile organic compounds (upstream oil and gas sector). Link to source: https://www.pembina.org/reports/2024-02-joint-methane-submission-eccc.pdf 

Project Drawdown. (2021). Climate solutions at work. Link to source: https://drawdown.org/publications/climate-solutions-at-work 

Project Drawdown. (2022). Legal job function action guide. Link to source: https://drawdown.org/programs/drawdown-labs/job-function-action-guides/legal 

Project Drawdown. (2023). Government relations and public policy job function action guide. Link to source: https://drawdown.org/programs/drawdown-labs/job-function-action-guides/government-relations-and-public-policy 

Project Drawdown. (2024, May 29). Unsung (climate) hero: The business case for curbing methane | presented by Stephan Nicoleau [video]. YouTube. Link to source: https://www.youtube.com/watch?v=Y5y0i-RMfJ0 

Ramya, A., Dhevagi, P., Poornima, R., Avudainayagam, S., Watanabe, M., & Agathokleous, E. (2023). Effect of ozone stress on crop productivity: A threat to food security. Environmental Research, 236(2), 116816. Link to source: https://doi.org/10.1016/j.envres.2023.116816 

Ravikumar, A. P., & Brandt, A. R. (2017). Designing better methane mitigation policies: The challenge of distributed small sources in the natural gas sector. Environmental Research Letters, 12(4), 044023. Link to source: https://doi.org/10.1088/1748-9326/aa6791

Rissman, J. (2021). Benefits of the build back better act’s methane fee. Energy Innovation. Link to source: https://energyinnovation.org/wp-content/uploads/2021/10/Benefits-of-the-Build-Back-Better-Act-Methane-Fee.pdf 

Sampedro, J., Waldhoff, S., Sarofim, M., & Van Dingenen, R. (2023). Marginal damage of methane emissions: Ozone impacts on agriculture. Environmental and Resource Economics, 84(4), 1095-1126. Link to source: https://doi.org/10.1007/s10640-022-00750-6 

Schiffner, D., Kecinski, M., & Mohapatra, S. (2021). An updated look at petroleum well leaks, ineffective policies and the social cost of methane in Canada’s largest oil-producing province. Climatic Change, 164(3-4). Link to source: https://doi.org/10.1007/s10584-021-03044-w

Schmeisser, L., Tecza, A., Huffman, M., Bylsma, S., Delang, M., Stanger, J., Conway, TJ, and Gordon, D. (2024). Fossil Fuel Operations Sector: Oil and Gas Production and Transport Emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org 

Shindell, D., Sadavarte, P., Aben, I., Bredariol, T. O., Dreyfus, G., Höglund-Isaksson, L., Poulter, B., Saunois, M., Schmidt, G. A., Szopa, S., Rentz, K., Parsons, L., Qu, Z., Faluvegi, G., & Maasakkers, J. D. (2024). The methane imperative. Frontiers. Link to source: https://www.frontiersin.org/journals/science/articles/10.3389/fsci.2024.1349770/full

Smith, C., Nicholls, Z. R. J., Armour, K., Collins, W., Forster, P., Meinshausen, M., Palmer, M. D., & Watanabe, M. (2021). The earth’s energy budget, climate feedbacks, and climate sensitivity supplementary material (climate change 2021: The physical science basis. Contribution of working group I to the sixth assessment report of the Intergovernmental Panel on Climate Change). Intergovernmental Panel on Climate Change (IPCC). Link to source: https://www.ipcc.ch/ 

Tai, A. P., Sadiq, M., Pang, J. Y., Yung, D. H., & Feng, Z. (2021). Impacts of surface ozone pollution on global crop yields: Comparing different ozone exposure metrics and incorporating co-effects of CO2. Frontiers in Sustainable Food Systems, 5, 534616. Link to source: https://doi.org/10.3389/fsufs.2021.534616 

Tradewater. (2023). Methane. Retrieved August 16, 2024, from Link to source: https://www.ogci.com/progress-report/building-towards-net-zero 

Tran, H., Polka, E., Buonocore, J. J., Roy, A., Trask, B., Hull, H., & Arunachalam, S. (2024). Air quality and health impacts of onshore oil and gas flaring and venting activities estimated using refined satellite‐based emissions. GeoHealth, 8(3), e2023GH000938. Link to source: https://doi.org/10.1029/2023GH000938 

UN Environment Program. (2021). Global methane assessment: Benefits and costs of mitigating methane emissions. Link to source: https://www.unep.org/resources/report/global-methane-assessment-benefits-and-costs-mitigating-methane-emissions 

UN Environment Program. (2024). An eye on methane: Invisible but not unseen. Link to source: https://www.unep.org/interactives/eye-on-methane-2024/ 

U.S. Department of Commerce, Commercial Law Development Programme. (2023). Methane abatement for oil and gas - handbook for policymakers. Link to source: https://cldp.doc.gov/sites/default/files/2023-09/CLDP%20Methane%20Abatement%20Handbook.pdf

U.S. Energy Information Administration. (2024). What countries are the top producers and consumers of oil? Link to source: https://www.eia.gov/tools/faqs/faq.php?id=709&t=6 

U.S. Environmental Protection Agency. (2019). Global non-CO2 greenhouse gas emission projections & mitigation 2015 - 2050. Link to source: https://www.epa.gov/ozone-layer-protection/transitioning-low-gwp-alternatives-residential-and-commercial-air

Van Dingenen, R., Crippa, M., Maenhout, G., Guizzardi, D., & Dentener, F. (2018). Global trends of methane emissions and their impacts on ozone concentrations. Joint Research Commission (European Commission). Link to source: https://op.europa.eu/en/publication-detail/-/publication/c40e6fc4-dbf9-11e8-afb3-01aa75ed71a1/language-en

Wang, J., Fallurin, J., Peltier, M., Conway, TJ, and Gordon, D. (2024). Fossil Fuel Operations Sector: Refining Emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org 

World Bank Group. (2023). What you need to know about abatement costs and decarbonization. Link to source: https://www.worldbank.org/en/news/feature/2023/04/20/what-you-need-to-know-about-abatement-costs-and-decarbonisation 

World Bank Group. (2024). Global flaring and methane reduction partnership (GFMR). Retrieved August 16, 2024, from Link to source: https://www.worldbank.org/en/programs/gasflaringreduction 

Credits

Lead Fellow

  • Jason Lam

Contributors

  • Ruthie Burrows, Ph.D.

  • James Gerber, Ph.D.

  • Yusuf Jameel, Ph.D.

  • Daniel Jasper

  • Alex Sweeney

Internal Reviewers

  • Aiyana Bodi

  • Hannah Henkin

  • Ted Otte

  • Amanda D. Smith, Ph.D.

  • Paul C. West, Ph.D.

  • James Gerber, Ph.D.

Effectiveness

Each Mt of methane that is not emitted avoids 81.2 million t CO₂‑eq on a 20-yr basis and 27.9 million t CO₂‑eq on a 100-yr basis (Smith et al., 2021). The GWP of methane is shown in Table 1. If the methane is burned (converted into CO₂ ), the contribution to climate change will still be less than that of methane released directly into the atmosphere. Methane abatement can have a more immediate impact on future global temperature rise because it has a larger and faster warming effect than CO₂. Mitigating methane emissions in the near term can give us more time for reducing GHG emissions in hard-to-abate sectors.

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Table 1. Effectiveness at reducing emissions.

Unit: t CO₂‑eq /Mt of methane abated

100-yr GWP 27,900,000
20-yr GWP 81,200,000
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Cost

The cost of methane abatement will vary depending on the type of O&G production, the methane content of the O&G resource, and the strategies used to address it. We averaged the costs for various abatement strategies; methane content is sufficiently high to utilize methane abatement strategies, and energy infrastructure is available to utilize abated methane. The initial cost to abate 1 Mt of methane is US$594 million, the revenue is about US$193 million, and the overall net savings over a 30-yr amortization period is US$173 million. This means that reducing O&G methane emissions offers a net economic gain for O&G producers. We were not able to find operating cost information for the solution, meaning the net economic gain may be lower in practice. 

We considered the baseline scenario where O&G producers do not have systems or practices in place to monitor or stop methane from escaping to the atmosphere and found very limited cost data. We assumed baseline costs to be 0 for initial costs, operational costs, and revenue because current practices and infrastructure are releasing methane to the atmosphere as a part of their existing cost of doing business. 

Many of the initial cost data for methane abatement come from studies estimating how much capital would be required to reach methane emission targets for the O&G industry. These costs are for the global scale of O&G methane abatement and not from the point of view of an individual O&G producer. These studies do not go into detail about the cost of specific abatement strategies or their potential revenues. The context and assumptions are difficult to identify, since the abatement strategies must be tailored to each site. Ocko et al (2021) noted that most (around 80%) of economically feasible methane abatement actions are from the O&G sector. 

Table 2 shows the costs per t CO₂‑eq. The value of the methane sold, instead of released, will often bring in revenue that covers the costs of abatement. Refer to the Appendix for information on the proportion of strategies that O&G producers could implement at low to no cost.

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Table 2. Net cost per unit of climate impact.

Unit: 2023 US$/t CO₂‑eq

median (100-yr basis) -6.20
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Learning Curve

Many of the technology solutions for reducing methane emissions are mature, and we were unable to find literature suggesting the costs to implement these solutions will fall in the future. There may be efficiencies to be gained in LDAR, but little research offers insights into the costs of LDAR programs (Delphi Group, 2017, ICF, 2016). 

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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as emergency brake, gradual, or delayed.

Manage OIl & Gas Methane is an EMERGENCY BRAKE climate solution. It has the potential to deliver a more rapid impact than gradual and delayed solutions. Because emergency brake solutions can deliver their climate benefits quickly, they can help accelerate our efforts to address dangerous levels of climate change. For this reason, they are a high priority.

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Caveats

Burning methane produces CO₂. Though the GWP is far less than that of releasing methane into the atmosphere, the practice still creates a negative climate impact. Depending on the type of O&G production, methane abatement is already practiced with natural gas production and is likely to bring added profit. However, oil producers who are not already producing methane for profit may not be able to abate methane at a profit. 

Avoiding fossil fuel extraction, transport, and use is the only way to permanently reduce emissions from O&G production. For many low- and middle-income countries (LMICs), O&G is the main source of energy, and it is challenging for them to completely eliminate O&G from their energy mix while they are simultaneously working to improve living standards. High-income countries can help LMICs develop clean energy infrastructure by providing financial and technological support. This will prevent new investments in O&G infrastructure (Laan, et al., 2024), which would result in ongoing emissions for decades. It would also allow LMICs a realistic pathway to transition away from their existing O&G usage. O&G demand must fall by 80% between 2022 and 2050 to stay in alignment with the net-zero emissions scenarios modeled by IEA (2023c). O&G methane abatement will decrease over time as the O&G industry produces less methane to be abated.

Our assessment does not include the impact of the CO₂ created from the destruction of methane.

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Current Adoption

We found little literature quantifying the current adoption of methane management; much of the methane abatement research revolves around the amount of methane that needs to be abated to reach certain climate targets. Based on data from Global Methane Initiative (GMI, 2024), 0 Mt of methane was abated in 2023 and is shown in Table 3.


GMI (2024) provided a conservative estimate of cumulative methane emissions abated each year, with a total of 153.6 Mt CO₂‑eq (5.51 Mt methane) abated as of 2023. The methane is given as a cumulative value to show the incremental increase in total methane abated and to avoid double counting methane abated. GMI members only cover 70% of human-caused methane emissions, and the organization does not capture methane mitigation that occurs outside of GMI members. This suggests that even in years where methane was abated, it would likely still be an underestimate of what may have actually occurred globally. The untapped potential for methane abatement suggests that O&G companies are investing in increasing natural gas production, which may be due to relatively smaller profits from abatement and nonbinding regulations (Shindell et al., 2024). 

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Table 3. Current (2023) adoption level.

Unit: Mt of methane abated/yr

median (50th percentile) 0
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Adoption Trend

Although there is little research specifically quantifying the adoption of methane abatement strategies over time, we estimate the average adoption trend in recent years to be about 0.35 Mt/yr of methane abated. To create this estimate, we relied on GMI analysis (GMI, 2024). GMI showed methane abatement gradually increasing from 2011 to 2023, then tapering off around 2020 and beginning to decrease among its member organizations. Table 4 shows the adoption trend for O&G methane abatement.

The IEA (2025) compiled country-level reporting for GHG emissions with data up to 2024. However, we were not able to use the data for the adoption trend because the changes in methane emissions could have been due to reasons other than methane abatement. In reality, methane emissions may be affected by multiple factors such as natural disasters, political conditions, changes in O&G demand, and changes in O&G industry practices.

Oil and Gas Climate Initiative (2023) data on methane abatement to date for 12 major O&G companies indicate that methane emissions decreased 50% from 2017 to 2022; however, we cannot assume the rest of the O&G industry has made the same level of progress. 

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Table 4. Adoption trend, 2011–2022.

Unit: Mt methane abated/yr

median (50th percentile) 0.35
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Adoption Ceiling

We found an adoption ceiling of 80.7 Mt/yr of methane based on the IEA’s (2025) estimate for total methane emissions from the O&G sector. We assumed that current O&G methane emissions would remain the same into the future with no changes in O&G production or demand. Table 5 shows the adoption ceiling for O&G methane abatement.

Even in the IEA’s (2023c) highest methane abatement energy scenario, only 93% of the methane emissions are reduced by 2050. This would still leave methane emissions being released into the atmosphere by the O&G sector. Reduced O&G production will reduce the amount of methane emissions produced by the O&G sector and consequently reduce the amount of methane that needs to be controlled with methane abatement. 

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Table 5. Adoption ceiling.

Unit: Mt methane abated/yr

median (50th percentile) 80.7
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Achievable Adoption

Based on the limited data available for current adoption and adoption trend, we expect 3.26–8.84 Mt/yr of methane abated. The Achievable – Low value aligns with the IEA (2023c) baseline energy scenario (STEPS), in which partial methane abatement is used but not all technically possible methane is abated. The Achievable – High value aligns with the IEA (2023c) baseline scenario (STEPS), in which full methane abatement is employed (all technically possible methane is abated). We determined this range by taking the total methane abated in these scenarios and dividing by the difference between the target year and 2024 to determine an average amount of methane abated each year to reach the scenario target. Under both scenarios, reduced demand for O&G would reduce methane emissions produced and lower the adoption ceiling possible for methane abatement. Even in scenarios where there is reduced O&G demand, methane abatement would still be required to control fugitive methane emissions from O&G infrastructure and limit global climate change. 

The amount of methane that can be abated varies greatly depending on how much methane the O&G industry produces. If O&G production remains steady, cumulative methane abatement could be 21–81 Mt, according to the IEA energy scenarios. If O&G demand drops 80% (IEA’s Net Zero Emissions scenario), total methane emissions would decline to 18 Mt, and the use of methane abatement would reduce methane emissions further by 17 Mt, leaving only 1 Mt of methane emitted in 2050. 

There has been growing interest from governments and academia to more accurately identify methane emissions using technologies such as satellite sensing (MethaneSat, 2024); UNEP (2024) has set up a monitoring and operator’s alliance group that will share best practices among O&G producers. This alliance group has identified more than 1,200 methane releases, but only 15 responses from government or companies provided detail about the source of the emissions or whether any mitigation action was considered or taken. This shows there are still many opportunities to abate methane emissions. 

More than 150 countries (representing 50% of the world’s human-caused methane emissions) have joined the Global Methane Pledge to reduce methane emissions 30% from 2020 to 2030 (UNEP, 2021). The IEA (2023b) found that many governments already have announced or put into place measures to cut methane emissions, so we expect global methane abatement to grow. 

Conrad et al. (2023) found that the emission inventories reported by the Alberta, Canada, government underestimate the methane emissions from the O&G sector, with a large portion coming from venting. These sources of methane are relatively easier to address and can allow the O&G sector to quickly reduce methane emissions. Table 6 shows the statistical low and high achievable ranges for O&G methane abatement based on different sources for future uptake of O&G methane abatement.

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Table 6. Achievable adoption.

Unit: Mt methane abated/yr

Current Adoption 0
Achievable – Low 3.26
Achievable – High 8.84
Adoption Ceiling 80.66
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We estimate that the O&G industry is currently abating approximately 0 Gt CO₂‑eq/yr on a 100-yr basis and 0 Gt CO₂‑eq/yr on a 20-yr basis using methane abatement strategies. 

As the O&G industry grows or shrinks its emissions, the amount of methane available to abate will change accordingly. If O&G demand and production stay constant to 2050, we estimate 0.09–0.25 Gt CO₂‑eq/yr of methane could be abated. 

However, if O&G demand drops, the methane abatement potential would drop because the O&G sector is producing less methane. This is projected in the different energy scenarios modeled by the IEA (2023). The range between the current O&G methane abatement and the adoption ceiling is shown in Table 7.

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Table 7. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 0
Achievable – Low 0.09
Achievable – High 0.25
Adoption Ceiling 2.25
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Additional Benefits

Air Quality and Health

Methane reacts with other pollutants to create ground-level ozone (Mar et al., 2022), and incomplete combustion of methane (Figure 2) releases other pollutants such as CO₂, carbon monoxide, black carbon, and volatile organic compounds (Fawole et al., 2016; Johnson and Coderre, 2012; Motte et al., 2021). These pollutants cause respiratory, reproductive, and neurological diseases; cancer; and premature death (Michanowicz et al., 2021; Motte et al., 2021; Tran et al., 2024), so reducing methane release can improve human health. Reducing or stopping flaring at a small number of the largest active sites can significantly reduce air pollution (Anejionu et al., 2015; Johnson and Coderre, 2012). Van Dingenen et al. (2018) estimate that ambitious methane reduction could prevent 70,000 to 130,000 ozone-related deaths worldwide each year.

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Figure 2. Air pollutants emitted along the O&G life cycle (Moore et al., 2014). BTEX = benzene, toluene, ethylbenzene, xylene.

Diagram listing air pollutants emitted along the oil and gas life cycle

Source: Moore, C. W., Zielinska, B., Pétron, G., & Jackson, R. B. (2014). Air impacts of increased natural gas acquisition, processing, and use: A critical review. Environmental Science & Technology, 48(15), 8349–8359. Link to source: https://doi.org/10.1021/es4053472

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Food security

Methane reacts with chemicals like VOCs to form tropospheric, or ground-level ozone (Fiore et al., 2002). Ground-level ozone has been linked to reduced crop growth and yields (Mills et al., 2018; Samperdo et al., 2023; Tai et al., 2021). Mitigating methane emissions from O&G could improve food security by reducing ground-level ozone and its harmful impacts on agricultural productivity (Tai et al., 2014; Ramya et al., 2023).

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Risks

If natural gas prices drop there would be less economic reason for industries to voluntarily abate methane (IEA, 2021). Without policy support enforcing the use of methane abatement technologies, methane could continue to be released into the atmosphere. The use of methane abatement will be needed regardless of whether O&G demand remains the same or decreases over time because it has an immediate effect on reducing global temperature rise in the near term.

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Interactions with Other Solutions

Reinforcing

Managing O&G methane can reinforce other solutions that reduce the amount of methane released to the atmosphere. The use of solutions such as applying changes to operations and maintenance; converting, replacing, and installing devices; and LDAR in the O&G industry can help demonstrate the effectiveness and economic case for methane abatement elsewhere and build momentum for adoption of methane abatement in other sectors. 

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Competing

Managing O&G methane has the potential to compete with solutions that provide clean electricity and solutions that focus on fuel switching in transportation because this solution increases O&G supply and can reduce the cost of O&G products. As a result, it could prolong the use of fossil fuels and slow down the transition to clean electricity.

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Dashboard

Solution Basics

Mt methane abated

t CO₂-eq (100-yr)/unit
2.79×10⁷
units/yr
Current 0 03.268.84
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0 0.090.25
US$ per t CO₂-eq
-6
Emergency Brake

CH₄, N₂O, BC

Trade-offs

Methane abatement could increase the use of O&G resources without a broader strategy to reduce reliance on O&G as an energy resource. The use of methane abatement strategies to extend the use of existing O&G infrastructure, or building new O&G infrastructure, will not result in a net decrease in emissions. Beck et al. (2020) found that more than 57% of the GHG emissions from the O&G supply chain are from methane emissions, while the rest is due to CO₂ emissions (15% from the extraction process and 28% from O&G energy use). Even with methane mitigation, continued use of O&G will generate CO₂ emissions and will contribute to global temperature rise. 

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Mt CO2–eq/yr
< 50
50–100
100–200
200–300
> 300
Refining
Production
Transport

Annual emissions from oil and gas sources, 2024

Globally, oil and gas sources, including production, refining, and transport, were responsible for 81 Mt out of the 354 Mt of anthropogenic methane emissions in 2024. This is equivalent to 2,250 Mt CO2-eq based on a 100-year GWP time scale. Methane emissions occur throughout the supply chain due to equipment imperfections, leaks, and intentional venting.

International Energy Agency. (2025). Global Methane tracker 2025: Data tools. Link to source: https://www.iea.org/data-and-statistics/data-tools/methane-tracker

Schmeisser, L., Tecza, A., Huffman, M., Bylsma, S., Delang, M., Stanger, J., Conway, TJ, and Gordon, D. (2024). Fossil fuel operations sector: Oil and gas production and transport emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org

Wang, J., Fallurin, J., Peltier, M., Conway, TJ, and Gordon, D. (2024). Fossil fuel operations sector: Refining emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org

Mt CO2–eq/yr
< 50
50–100
100–200
200–300
> 300
Refining
Production
Transport

Annual emissions from oil and gas sources, 2024

Globally, oil and gas sources, including production, refining, and transport, were responsible for 81 Mt out of the 354 Mt of anthropogenic methane emissions in 2024. This is equivalent to 2,250 Mt CO2-eq based on a 100-year GWP time scale. Methane emissions occur throughout the supply chain due to equipment imperfections, leaks, and intentional venting.

International Energy Agency. (2025). Global Methane tracker 2025: Data tools. Link to source: https://www.iea.org/data-and-statistics/data-tools/methane-tracker

Schmeisser, L., Tecza, A., Huffman, M., Bylsma, S., Delang, M., Stanger, J., Conway, TJ, and Gordon, D. (2024). Fossil fuel operations sector: Oil and gas production and transport emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org

Wang, J., Fallurin, J., Peltier, M., Conway, TJ, and Gordon, D. (2024). Fossil fuel operations sector: Refining emissions [Data set]. RMI, Climate TRACE Emissions Inventory. Retrieved April 18, 2025 from Link to source: https://climatetrace.org

Maps Introduction

Methane abatement is recommended for all oil and gas (O&G) production. The levels of achievable abatement can vary geographically, depending on the extraction technology used (i.e., conventional drilling versus hydraulic fracturing). The Middle East, Europe, Asia, and North America are among the largest O&G producers and have the highest related methane emissions, according to the IEA (2025). Research from Shindell et al. (2024) found that North America, Russia, and several countries in the Middle East and Africa have the most methane abatement potential in O&G. O&G methane abatement could be accelerated if technologies and strategies used in high-income countries are shared with other O&G producing countries.

Action Word
Manage
Solution Title
Oil & Gas Methane
Classification
Highly Recommended
Lawmakers and Policymakers
  • Hold well owners accountable for harm caused to the public and environment.
  • Introduce performance goals for emissions reductions.
  • Use economic measures such as taxes or financial incentives.
  • Regulate key aspects of abatement, such as the use of LDAR, and enforce existing regulations.
  • Utilize data-driven public information programs such as collecting and publishing monitoring and reporting data (“naming and shaming”).
  • Distribute information to operators, such as technology options that fit relevant regulations. 

Further information:

Practitioners
  • Shift business models toward 100% renewable energy.
  • Detect and repair methane leaks.
  • Implement device conversion, replacement, and installation and LDAR.
  • Change operations and maintenance practices to reduce or recover vented methane.
  • Implement zero-tolerance policies for methane leaks.
  • Increase transparency on emissions and practices.
  • Join cross-company and industry coalitions that facilitate implementation.

Further information:

Business Leaders
  • Eliminate major methane O&G emitters in your value chains or pressure them to improve performance.
  • Create a plan to transition to renewable energy.
  • Center methane in net-zero strategies, such as establishing internal methane pricing mechanisms and requiring suppliers to meet standards for monitoring and reducing methane emissions in your operations.
  • Identify technology partners that are monitoring and reducing methane emissions and make market commitments.
  • If your company is participating in the voluntary carbon market, look into funding projects that plug methane leaks.
  • Proactively collaborate with government and regulatory actors to support methane abatement policies.
  • Join or support transparency initiatives led by trusted third parties, such as the Oil and Gas Methane Partnership 2.0.

Further information:

Nonprofit Leaders
  • Help with monitoring and reporting by, for example, utilizing satellite data.
  • Help design policies and regulations that support methane abatement.
  • Educate the public on the urgent need to abate methane.
  • Join or support efforts such as the Global Methane Alliance.
  • Encourage policymakers to create ambitious targets and regulations.
  • Pressure O&G companies to improve their practices.
  • Take or support legal action when companies do not follow relevant regulations.
  • Work with journalists and the media to support public education on the importance of methane abatement.

Further information:

Investors
  • Pressure and influence portfolio companies to incorporate methane abatement into their operations, noting that this saves money and adds value for investors.
  • Provide capital for nascent methane abatement strategies and leak detection and monitoring instruments.
  • Invest in green bonds and other financial instruments that support methane abatement projects.
  • Seek impact investment opportunities such as sustainability-linked loans in entities that set methane abatement targets.
  • Invest in projects that plug methane leaks. 

Further information:

Philanthropists and International Aid Agencies
  • Provide capital for methane monitoring, de-risking, and abatement in the early stages of implementation.
  • Support global, national, and local policies that reduce methane emissions.
  • Support accelerators or multilateral initiatives like the Global Methane Hub.
  • If working in a fossil fuel–producing nation, support sustainable developments in other sectors of the economy.
  • Explore opportunities to fund the plugging of abandoned oil or gas wells that leak methane.
  • Advance awareness of the public health and climate threats from the O&G industry.
  • Join, create, or participate in partnerships or certification programs dedicated to managing oil and gas methane.

Further information:

Thought Leaders
  • Provide technical assistance (e.g., monitoring and reporting) to businesses, government agencies, and other entities working to reduce methane emissions.
  • Help design policies and regulations that support methane abatement.
  • Analyze historical emissions patterns to identify and publicize successful programs.
  • Educate the public on the urgent need to abate methane.
  • Advocate to policymakers for more ambitious targets and regulations.
  • Pressure O&G companies to improve their practices.
  • Join, create, or participate in partnerships or certification programs dedicated to managing oil and gas methane.

Further information:

Technologists and Researchers
  • Develop new LDAR technologies that reduce cost and required capacity.
  • Develop new technologies for measuring and verifying emissions.
  • Conduct longitudinal studies to measure emissions against objectives or means of enforcement. 

Further information:

Communities, Households, and Individuals
  • If you are impacted by harmful O&G methane management practices, document your experiences.
  • Reduce household consumption of fossil fuels by adopting clean energy sources, increasing energy efficiency, and replacing fossil fuel-powered equipment with electricity-powered equipment.
  • Share documentation of harmful practices and/or other key messages with policymakers, the press, and the public.
  • Encourage policymakers to improve regulations.
  • Support public education efforts on the urgency and need to address the issue.

Further information:

Sources
Evidence Base

Consensus of effectiveness of abating methane emissions in the O&G sector: High

There is a high level of consensus about the effectiveness of methane abatement strategies. These strategies can be deployed cost effectively in many cases and have an immediate impact on reducing global temperature rise. 

Authoritative sources such as the IEA (2023d), UNEP (2021), and Global Methane Hub (2024) agree that reducing methane emissions can noticeably reduce the rate of global temperature rise. DeFabrizio et al. (2021) identified that methane abatement strategies such as LDAR, switching from natural gas fuel to electric power, using air for pneumatic devices, and using vapor recovery units could reduce O&G methane emissions by 40% by 2030 based on global 2017 O&G emissions. With methane being the second largest contributor to climate change after CO₂, reductions in methane emissions can quickly reduce global temperature rise.

Others (Marks Levi, 2022; DeFabrizio et al., 2021; Malley et al., 2023) have identified that many methane abatement strategies can use existing technologies, often at low cost. Dunsky (2023) found that implementing 24 of the least expensive abatement measures in the exploration and production phases of Canada’s O&G industry could help Canada achieve its 2030 methane target. The IEA (2023a) noted that the O&G industry was responsible for 80 Mt of methane in 2022 and had the largest potential for abatement in the near term. The O&G industry has the potential to abate 60 Mt of methane by 2030 using abatement strategies; 40% of that could be abated at no net cost based on average natural gas prices from 2017 to 2021 (IEA, 2023a).

The results presented in this document summarize findings from more than 15 reviews and meta-analyses and more than 10 original studies reflecting current evidence from two countries, primarily from the United States and Canada, and from global sources. We recognize this limited geographic scope creates bias, and hope this work inspires research and data-sharing on this topic in underrepresented regions.

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Appendix

Data describing methane abatement potential in the O&G industry are often shown in marginal abatement cost curves (MACCs), which incorporate the initial cost, operating cost, revenue, and any extra costs per unit of emissions reduced as one value.

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Figure A1. Marginal abatement cost curves (MACC) for methane abatement in the O&G industry (IEA, 2024).

Cost curve chart.

Source: International Energy Agency (Global Methane Tracker 2024).

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MACCs indicate a range of potential climate actions and show at a glance the magnitude of financial return or financial cost across that range. In Figure A1, for the blocks below the horizontal axis, the value received from the sale of the captured methane is greater than the cost of the solution employed. The width of a block shows the annual amount of emissions a technology can abate, with wider blocks abating more emissions than narrower blocks.

MACCs are useful for identifying which climate action could have the most impact at reducing emissions or which options have a net economic gain. However, they do not illustrate the intricacies that may be in play among different climate actions and can lead users to ignore hard-to-abate emissions. The World Bank (2023) identified that MACCs are useful to find which option will reduce emissions by a set percentage but less useful for reducing absolute emissions to near zero. 

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Manage Coal Mine Methane

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Summary

Managing coal mine methane (CMM) is the process of reducing methane emissions released from coal deposits and surrounding rock layers due to mining activities. CMM is naturally found in coal seams and released into the atmosphere when the coal seams are disturbed. Coal mines can continue to emit methane even after being closed or abandoned, which is known as abandoned mine methane (AMM). CMM and AMM can be captured and then utilized as a fuel source or destroyed before they reach the atmosphere [U.S. Environmental Protection Agency (EPA), 2024a].

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Description for Social and Search
Managing coal mine methane (CMM) is the process of reducing methane emissions released from coal deposits and surrounding rock layers due to mining activities.
Overview

CMM is released from coal mines before, during, and after active coal mining and from coal being transported (EPA, 2024a). Atmospheric methane has a GWP of 81 on a 20-yr basis and a GWP of 28 on a 100-yr basis (Intergovernmental Panel on Climate Change [IPCC], 2023). This means methane is 81 times more effective at trapping heat than CO₂. Because methane is a short-lived climate pollutant that has a much stronger warming effect than CO₂ over a given time period, abating methane from coal mines will have a powerful near-term impact on slowing global climate change. If capturing methane is not possible, destroying the methane by burning it is preferable to releasing it.

CMM comes from five major sources throughout the coal mine’s life cycle (Figure 1): 

  1. Degasification systems – pipes installed in the ground to move methane into the atmosphere before starting mining
  2. Ventilation air – air escaping from underground mines when fresh air is used to push out underground methane during mining
  3. Surface mines – exposed coal seams that emit methane directly into the atmosphere during mining
  4. Fugitive emissions – already mined coal that emits methane while being transported or stored
  5. Abandoned or closed mines – coal seams and rock strata that are exposed to air, allowing AMM to escape through existing vents or cracks after mine closure. 

Figure 1. Percent breakdown of CMM sources in the United States, 2021.

Source: U.S. Environmental Protection Agency (2024d). Sources of coal mine methane. Retrieved November 5, 2024. https://www.epa.gov/cmop/sources-coal-mine-methane

CMM management relies on several practices and technologies to reduce the amount of methane released into the atmosphere. The CMM that is captured can be used as a fuel at high concentrations and destroyed through flaring or oxidation at low concentrations. The methane captured from degasification systems typically has a high concentration while fugitive and ventilation methane sources are low concentration. CMM management also includes leak detection and repair using satellites, drones, or other technologies to prevent methane from escaping into the atmosphere.

Underground coal mines have more methane abatement strategies available due to higher average methane concentrations and relative ease of capture. Surface coal mines are exposed directly to the atmosphere and can cover large areas, making them more difficult to abate methane, though there are technologies that can reduce CMM emissions. See the Appendix for more details on the abatement technologies specific to underground and surface coal mines.

Assan, S., & Whittle, E. (2023). In the dark: Underreporting of coal mine methane is a major climate risk. Ember. Link to source: https://ember-energy.org/latest-insights/in-the-dark-underreporting-of-coal-mine-methane-is-a-major-climate-risk/#supporting-material 

Assan, S. (2024). Understanding the EU’s methane regulation for coal. Ember. Link to source: https://ember-energy.org/latest-insights/eumethane-reg-explained/ 

CNX. (2024, March 20). Jumpstarting coal mine methane capture projects for beneficial end use [PowerPoint slides].Global Methane Initiative. Link to source: https://www.globalmethane.org/resources/details.aspx?resourceid=5386 

DeFabrizio, S., Glazener, W., Hart, C., Henderson, K., Kar, J., Katz, J., Pratt, M. P., Rogers, M., Ulanov, A., & Tryggestad, C. (2021). Curbing methane emissions: How five industries can counter a major climate threat. McKinsey Sustainability. Link to source: https://www.mckinsey.com/~/media/mckinsey/business%20functions/sustainability/our%20insights/curbing%20methane%20emissions%20how%20five%20industries%20can%20counter%20a%20major%20climate%20threat/curbing-methane-emissions-how-five-industries-can-counter-a-major-climate-threat-v4.pdf 

Domingo, N. G. G., Fiore, A. M., Lamarque, J.-F., Kinney, P. L., Jiang, L., Gasparrini, A., Breitner, S., Lavigne, E., Madureira, J., Masselot, P., das Neves Pereira da Silva, S., Sheng Ng, C. F., Kyselý, J., Guo, Y., Tong, S., Kan, H., Urban, A., Orru, H., Maasikmets, M., … Chen, K. (2024). Ozone-related acute excess mortality projected to increase in the absence of climate and air quality controls consistent with the Paris Agreement. One Earth (Cambridge, Mass.), 7(2), 325–335. Link to source: https://doi.org/10.1016/j.oneear.2024.01.001

Fiore, A. M., Jacob, D. J., & Field, B. D. (2002). Linking ozone pollution and climate change: The case for controlling methane. Geophysical Research Letters, 29(19), 182-197. Link to source: https://doi.org/10.1029/2002GL015601 

Gajdzik, B., Tobór-Osadnik, K., Wolniak, R., & Grebski, W. W. (2024). European climate policy in the context of the problem of methane emissions from coal mines in Poland. Energies, 17(10), 2396. Link to source: https://doi.org/10.3390/en17102396 

Global Energy Monitor (n.d.). Global coal mine tracker. Retrieved February 27, 2025 from Link to source: https://globalenergymonitor.org/projects/global-coal-mine-tracker/ 

Global Methane Initiative. (2015). Coal mine methane country profiles. Link to source: https://www.globalmethane.org/documents/toolsres_coal_overview_fullreport.pdf 

Global Methane Initiative (2018). Expert dialogue on ventilation air methane (VAM). Link to source: https://www.globalmethane.org/documents/res_coal_VAM_Dialogue_Report_20181025.pdf 

Global Methane Initiative (2024a). 2023 Accomplishments in methane mitigation, recovery, and use through U.S.-supported international efforts. Link to source: https://www.epa.gov/system/files/documents/2024-12/epa430r24009-fy23-accomplishments-report.pdf 

Global Methane Initiative (2024b). International coal mine methane project list. Link to source: https://globalmethane.org/resources/details.aspx?resourceid=1981 

Hong, C., Mueller, N. D., Burney, J. A., Zhang, Y., AghaKouchak, A., Moore, F. C., Qin, Y., Tong, D., & Davis, S. J. (2020). Impacts of ozone and climate change on yields of perennial crops in California. Nature Food, 1(3), 166–172. Link to source: https://doi.org/10.1038/s43016-020-0043-8 

Intergovernmental Panel on Climate Change (IPCC). (2023). In: Climate change 2023: Synthesis report. Contribution of working groups I, II and III to the sixth assessment report of the intergovernmental panel on climate change [core writing team, H. Lee and J. Romero (eds.)]. IPCC, Geneva, Switzerland, pp. 1–34, doi: 10.59327/IPCC/AR6-9789291691647.001 Link to source: https://www.ipcc.ch/report/ar6/syr/ 

International Energy Agency. (2021). Global methane tracker 2021: Methane abatement and regulation. Link to source: https://www.iea.org/reports/methane-tracker-2021/methane-abatement-and-regulation 

International Energy Agency. (2023a). Net zero roadmap: A global pathway to keep the 1.5℃ goal in reach - 2023 update. Link to source: https://www.iea.org/reports/net-zero-roadmap-a-global-pathway-to-keep-the-15-0c-goal-in-reach 

International Energy Agency. (2023b). Strategies to reduce emissions from coal supply. Global Methane Tracker 2023. Link to source: https://www.iea.org/reports/global-methane-tracker-2023/strategies-to-reduce-emissions-from-coal-supply 

International Energy Agency. (2023c). The imperative of cutting methane from fossil fuels. Link to source: https://www.iea.org/reports/the-imperative-of-cutting-methane-from-fossil-fuels 

International Energy Agency. (2023d). Global methane tracker 2023: Overview. Link to source: https://www.iea.org/reports/global-methane-tracker-2023/overview 

International Energy Agency. (2024a). Global methane tracker documentation 2024 version. Link to source: https://iea.blob.core.windows.net/assets/d42fc095-f706-422a-9008-6b9e4e1ee616/GlobalMethaneTracker_Documentation.pdf 

International Energy Agency. (2024b). Methane tracker: Data tools. Link to source: https://www.iea.org/data-and-statistics/data-tools/methane-tracker 

International Energy Agency. (2024c). World energy outlook 2024. Link to source: https://www.iea.org/reports/world-energy-outlook-2024 

International Energy Agency. (2025). Global methane tracker documentation 2025 version. Link to source: https://iea.blob.core.windows.net/assets/2c0cf2d5-3910-46bc-a271-1367edfed212/GlobalMethaneTracker2025.pdf 

Kholod, N., Evans, M., Pilcher, R. C., Roshchanka, V., Ruiz, F., Coté, M., & Collings, R. (2020). Global methane emissions from coal mining to continue growing even with declining coal production. Journal of Cleaner Production, 256. Link to source: https://doi.org/10.1016/j.jclepro.2020.120489 

Lewis, C., Tate, R.D., and Mei, D.L. (2024). Fuel operations sector: Coal mining emissions methodology [Data set]. WattTime and Global Energy Monitor, Climate TRACE Emissions Inventory. Retrieved April 18, 2025, from Link to source: https://climatetrace.org 

Malley, C. S., Borgford-Parnell, N. Haeussling, S., Howard, L. C., Lefèvre E. N., & Kuylenstierna J. C. I. (2023). A roadmap to achieve the global methane pledge. Environmental Research: Climate, 2(1). Link to source: https://doi.org/10.1088/2752-5295/acb4b4 

Mar, K. A., Unger, C., Walderdorff, L., & Butler, T. (2022). Beyond CO2 equivalence: The impacts of methane on climate, ecosystems, and health. Environmental Science & Policy, 134, 127–136. Link to source: https://doi.org/10.1016/j.envsci.2022.03.027 

MethaneSAT. (2024). Solving a crucial climate challenge. Retrieved September 2, 2024 Link to source: https://www.methanesat.org/satellite/ 

Mills, G., Sharps, K., Simpson, D., Pleijel, H., Frei, M., Burkey, K., Emberson, L., Cuddling, J., Broberg, M., Feng, Z., Kobayashi, K. & Agrawal, M. (2018). Closing the global ozone yield gap: Quantification and cobenefits for multistress tolerance. Global Change Biology, 24(10), 4869–4893. Link to source: https://doi.org/10.1111/gcb.14381 

Ocko, I. B., Sun, T., Shindell, D., Oppenheimer, M. Hristov, A. N., Pacala, S. W., Mauzerall, D. L., Xu, Y. & Hamburg, S. P. (2021). Acting rapidly to deploy readily available methane mitigation measures by sector can immediately slow global warming. Environmental Research, 16(5). Link to source: https://doi.org/10.1088/1748-9326/abf9c8 

Ramya, A., Dhevagi, P., Poornima, R., Avudainayagam, S., Watanabe, M., & Agathokleous, E. (2023). Effect of ozone stress on crop productivity: A threat to food security. Environmental Research, 236(2), 116816. Link to source: https://doi.org/10.1016/j.envres.2023.116816 

Roshchanka, V., Evans, M., Ruiz, F., & Kholod, N. (2017). A strategic approach to selecting policy mechanisms for addressing coal mine methane emissions: A case study on Kazakhstan. Environmental Science & Policy, 78, 185–192. Link to source: https://doi.org/10.1016/j.envsci.2017.08.005 

Roshchanka, V., & Talkington, C. (2022). Effective monitoring, reporting and verification of methane emissions in the coal industry and the linkage to methane mitigation. Link to source: https://papers.ssrn.com/sol3/papers.cfm?abstract_id=4298409

Rystad Energy. (2023, October 18). Methane tracking technologies study [PowerPoint slides]. Environmental Defense Fund. Link to source: https://www.edf.org/sites/default/files/documents/Methane%20Tracking%20Technologies%20Study%20Oct%2018%202023.pdf 

Sampedro, J., Waldhoff, S., Sarofim, M., & Van Dingenen, R. (2023). Marginal damage of methane emissions: Ozone impacts on agriculture. Environmental and Resource Economics, 84(4), 1095–1126. Link to source: https://doi.org/10.1007/s10640-022-00750-6 

Setiawan, D. & Wright, C. (2024). The risks of ignoring methane emissions in coal mining. Ember. Link to source: https://ember-energy.org/latest-insights/the-risks-of-ignoring-methane-emissions-in-coal-mining/#supporting-material 

Shindell, D., Sadavarte, P., Aben, I., Bredariol, T. O., Dreyfus, G., Höglund-Isaksson, L., Poulter, B., Saunois, M., Schmidt, G. A., Szopa, S., Rentz, K., Parsons, L., Qu, Z., Faluvegi, G., & Maasakkers, J. D. (2024). The methane imperative. Frontiers. Link to source: https://www.frontiersin.org/journals/science/articles/10.3389/fsci.2024.1349770/full

Silvia, F., Talia, V., & Di Matteo, M. (2021). Coal mining and policy responses: Are externalities appropriately addressed? A meta-analysis. Environmental Science & Policy, 126, 39–47. Link to source: https://doi.org/10.1016/j.envsci.2021.09.013

Smith, C., Nicholls, Z. R. J., Armour, K., Collins, W., Forster, P., Meinshausen, M., Palmer, M. D., & Watanabe, M. (2021). The earth’s energy budget, climate feedbacks, and climate sensitivity supplementary material (climate change 2021: The physical science basis. Contribution of working group I to the sixth assessment report of the Intergovernmental Panel on Climate Change). Intergovernmental Panel on Climate Change (IPCC). Link to source: https://www.ipcc.ch/ 

Tai, A. P., Sadiq, M., Pang, J. Y., Yung, D. H., & Feng, Z. (2021). Impacts of surface ozone pollution on global crop yields: comparing different ozone exposure metrics and incorporating co-effects of CO2. Frontiers in Sustainable Food Systems, 5, 534616. Link to source: https://doi.org/10.3389/fsufs.2021.534616 

Tao, S., Chen, S., & Pan, Z. (2019). Current status, challenges, and policy suggestions for coalbed methane industry development in China: A review. Energy Science & Engineering, 7(4), 1059–1074. Link to source: https://doi.org/10.1002/ese3.358

Tate, R. D., (2022). Bigger than oil or gas? Sizing up coal mine methane. Global Energy Monitor. Link to source: https://globalenergymonitor.org/wp-content/uploads/2022/03/GEM_CCM2022_final.pdf 

United Nations Economic Commission for Europe (UNECE). (2019). Best practice guidance for effective methane recovery and use from abandoned coal mines. Link to source: https://unece.org/fileadmin/DAM/energy/images/CMM/CMM_CE/Best_Practice_Guidance_for_Effective_Methane_Recovery_and_Use_from_Abandoned_Coal_Mines_FINAL__with_covers_.pdf 

United Nations Economic Commission for Europe (UNECE). (2022). Best practice guidance for effective management of coal mine methane at national level: Monitoring, reporting, verification and mitigation. Link to source: https://globalmethane.org/documents/Best%20Practice%20Guidance%20for%20Effective%20Management%20of%20Coal%20Mine%20Methane%20at%20National%20Level%20Monitoring,%20Reporting,%20Verification%20and%20Mitigation.pdf 

United Nations Environment Program. (2022). Coal mine methane science studies road map. Link to source: https://www.unep.org/resources/other-evaluation-reportsdocuments/coal-mine-methane-science-studies-road-map 

U.S. Center for Disease Control and Prevention, (2024, September 25). Mining fires and explosions. Link to source: https://www.cdc.gov/niosh/mining/topics/fires-explosions.html 

U.S. Environmental Protection Agency (2019). Global non-CO2 greenhouse gas emission projections & mitigation 2015–2050. Link to source: https://www.epa.gov/sites/default/files/2019-09/documents/epa_non-co2_greenhouse_gases_rpt-epa430r19010.pdf 

U.S. Environmental Protection Agency (2024a). About coal mine methane. Retrieved November 5, 2024. Link to source: https://www.epa.gov/cmop/about-coal-mine-methane 

U.S. Environmental Protection Agency (2024b). Coalbed methane outreach program accomplishments. Link to source: https://www.epa.gov/cmop/coalbed-methane-outreach-program-accomplishments 

U.S. Environmental Protection Agency (2024c). GHGRP underground coal mines. Retrieved November 5, 2024. Link to source: https://www.epa.gov/ghgreporting/ghgrp-underground-coal-mines 

U.S. Environmental Protection Agency (2024d). Sources of coal mine methane. Retrieved November 5, 2024. Link to source: https://www.epa.gov/cmop/sources-coal-mine-methane 

Ward, K., Mountain State Spotlight, Mierjeski, A. & Scott Pham. (2023). In the game of musical mines, environmental damage takes a back seat. ProPublica. Link to source: https://www.propublica.org/article/west-virginia-coal-blackjewel-bankruptcy-pollution 

Zhu, R., Khanna, N., Gordon, J., Dai, F., & Lin, J. (2023). Abandoned coal mine methane reduction. Berkeley Lab. Link to source: https://ccci.berkeley.edu/sites/default/files/Abandonded%20Coal%20Mines_Final%20%28EN%29.pdf 

Credits

Lead Fellow

  • Jason Lam

Contributors

  • James Gerber, Ph.D.

  • Yusuf Jameel, Ph.D. 

  • Ruthie Burrows, Ph.D.

  • Daniel Jasper

  • Alex Sweeney

Internal Reviewers

  • Sarah Gleeson, Ph.D.

  • Aiyana Bodi

  • Hannah Henkin

  • Ted Otte

  • Amanda D. Smith, Ph.D.

  • Paul C. West, Ph.D.

Effectiveness

Each Mt of methane that is not emitted avoids 81.2 Mt CO₂‑eq on a 20-yr basis and 27.9 Mt CO₂‑eq on a 100-yr basis (Smith et al., 2021). The GWP of methane is shown in Table 1. If the methane is converted into CO₂ through burning the contribution to global climate change will still be less than if the methane were released into the atmosphere. Methane abatement can have a more immediate impact on future global temperature rise because it has a larger and faster warming effect than CO₂. Mitigating methane emissions in the near term can give us more time for reducing GHG emissions in hard-to-abate sectors.

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Table 1. Effectiveness at reducing emissions.

Unit: t CO₂‑eq/Mt methane abated

100-yr GWP 27,900,000
20-yr GWP 81,200,000
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Cost

The cost of methane abatement will vary depending on the type of coal mine, the methane content of the coal seam, the strategies used, and the availability of financial support for methane abatement. For our analysis, we average the costs for various feasible abatement strategies under two general assumptions: sufficiently high methane content for any of the major abatement strategies to be applied (IEA, 2024a) and the ability to use the abated methane on-site or sell it to natural gas companies. The initial cost to abate 1 Mt of methane is US$1.5 billion, the operating cost is about US$130 million, revenue is about US$260 million and the overall net savings over a 30-yr amortization period is US$90 million. We were only able to find revenue information from the IEA (2023b, 2024a), meaning the net cost could be different than shown here due to the site specific nature of methane abatement strategies. 

We considered the baseline scenario to be coal mining practices without methane abatement; all cost estimates here are relative to that scenario.

Cost data were limited for this solution. The available costs for a specific abatement strategy were normalized according to the cost of abating one Mt of methane, and it was assumed that a single strategy abated all of the methane for the coal mine. This results in an overestimate of the effectiveness of any individual strategy. In reality, multiple strategies are likely to be used. The costs shown in Table 2 are for the global scale of coal methane abatement and not from the point of view of an individual coal producer. Many studies that look at global coal methane abatement put multiple abatement strategies together and do not go into detail about the individual technology costs. The IEA (2024a) included costs for individual CMM abatement strategies; however, the costs were only applicable for coal mines that produce enough methane for it to be economically feasible to deploy the specific abatement strategy. Flaring is an effective strategy for destroying captured methane, but will not create revenue in the absence of a carbon market. For more details on important aspects for coal methane abatement strategies, refer to the Appendix.

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Table 2. Cost per unit climate impact.

Unit: 2023 US$/t CO₂‑eq, 100-yr basis

median -3.17
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Learning Curve

Many of the solutions for reducing methane emissions from coal mining are mature. Research from Rystad (2023) found that technologies for abating CMM emissions, such as drainage gas utilization, sealing and rerouting, and flaring, were considered mature in Australian coal mines. Regenerative thermal oxidation technology is in commercial use for destroying volatile organic compounds and can be used for destroying ventilation air methane (VAM), but the manufacturers have little interest in improving the technology for use in coal mines without confirmed markets (GMI, 2018; Rystad, 2023). We do not foresee the costs of implementing these solutions falling in the future. CMM regulations may encourage manufacturers to improve oxidation technology, but the technology is already used commercially, so there may not be large efficiency gains.

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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as emergency brake, gradual, or delayed.

Manage Coal Mine Methane is an EMERGENCY BRAKE climate solution. It has the potential to deliver a more rapid impact than gradual and delayed solutions. Because emergency brake solutions can deliver their climate benefits quickly, they can help accelerate our efforts to address dangerous levels of climate change. For this reason, they are a high priority.

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Caveats

CMM abatement consists of capturing methane that would otherwise be released into the atmosphere. If the methane is burned, CO₂ will be emitted as a byproduct; however, this provides a net climate benefit compared to the methane that would be emitted. CMM emissions management can be avoided by not extracting, transporting, or using coal in the first place. 

As coal demand drops, the number of closed or abandoned coal mines will increase. These mines will continue to release AMM into the atmosphere for many decades. Sealing underground mines can stop methane from being released, but seals have been known to fail and require ongoing monitoring to verify methane is not escaping (Kholod et al., 2020). Gas collection systems can be used to capture AMM, but the CO₂ produced will need to be captured for complete emission reductions. Flooding underground coal mines is very effective at stopping methane from being released; however, there are concerns about water contamination (McKinsey, 2021).

Our assessment does not include the impact of the CO₂ created from the destruction of methane.

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Current Adoption

We estimated that the coal sector abated 0.59 Mt of methane in 2023 and released 40 Mt in 2024 (IEA, 2025). Reports from EPA (2022), and GMI (2023) estimated the amount of CMM abated to date, and the statistical ranges from the sources are shown in Table 3. However, most of the data focused on coal mines in the United States. The EPA (2024b) stated that 0.3 Mt of methane was captured in 2021 due to the Coalbed Methane Outreach Program. CMM is controlled at coal mines for health and safety reasons, but only in 2024 was regulation introduced for reducing methane emissions from the energy sector in the European Union (Assan, 2024).


GMI (2024a) reports that 0.79 Mt of methane was abated from coal mines in 2023 among its member countries. The organization includes 48 GMI member countries but covers only 70% of human-caused methane emissions and does not track methane mitigation that has occurred outside of the group. GMI (2024b) currently lists more than 471 CMM abatement projects in 20 countries worldwide. According to Global Energy Monitor (n.d.), over 6,000 coal mines were active in more than 70 countries as of April 2024. With these data sources, we consider our analysis of the current adoption of CMM abatement as conservative. 

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Table 3. Current (2023) adoption level.

Unit: Mt/yr of methane abated

25th percentile 0.49
mean 0.59
median (50th percentile) 0.59
75th percentile 0.69
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Adoption Trend

Although there are little data specifically quantifying the adoption trend of methane abatement strategies, we estimate the median adoption trend to be about 0.60 Mt/yr of methane abated.  Table 4 shows the adoption trend for CMM abatement.

GMI (2024) reported methane abatement staying relatively stable from 2016 to 2023 at about 0.8 Mt/yr, with a small increase to 1.0 Mt of methane in 2019–2022 before decreasing back to 0.8 Mt in 2023, causing the adoption trend to be higher than the current adoption value we state above. The EPA (2024a) Coalbed Methane Outreach Program showed fairly stable emission reductions of around 0.33 Mt/yr between 2016 and 2022. The annual methane emission abatement from this program gradually increased 2003–2011, followed by a continued trend of methane abatement at a slower rate 2011–2022. The IEA (2024b) found that almost 2.0 Mt of methane was emitted in 2023 by the United States coal industry, and 60% of those emissions could be abated.

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Table 4. (2016–2023) adoption trend.

Unit: Mt/yr methane abated

25th percentile 0.46
mean 0.60
median (50th percentile) 0.60
75th percentile 0.73
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Adoption Ceiling

We found an adoption ceiling of about 40.3 Mt/yr of methane based on the IEA’s (2025) estimate for total methane emissions from the coal mine sector. We assumed that current CMM emissions would remain the same into the future with no changes in coal production or demand. Table 5 shows the adoption ceiling for coal mine methane abatement.

Even in the IEA’s (2023c) highest methane abatement energy scenario, only 93% of the methane emissions are reduced by 2050. This would still leave the coal sector releasing methane into the atmosphere. Reduced coal production will reduce the amount of methane emissions produced by the coal sector and consequently reduce the amount of methane that needs to be controlled with methane abatement. However, methane abatement will still be important for abating the remaining CMM emissions and the growing proportion of AMM emissions (IEA, 2023c, Kholod et al., 2020). 

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Table 5. Adoption ceiling.

Unit: Mt/yr of methane abated

median (50th percentile) 40.30
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Achievable Adoption

The amount of methane that could be abated from CMM varies greatly depending on global coal demand. We estimate an achievable adoption range of 2.83–4.40 Mt/yr of methane abated.The Achievable – Low value aligns with the IEA (2023c) Announced Pledges scenario, in which all announced climate policies are met and full methane abatement is employed, but net-zero emissions are not achieved. This range of high and low values was determined by taking the total methane abated in these scenarios and dividing by the difference between the target year and 2024 to determine an average amount of methane abated each year to reach the scenario target. 

The Achievable – High value aligns with Ocko et al.(2021), where all economically and technically feasible methane abatement is employed by 2030. DeFabrizio et al. (2021) estimated that the degasification of underground mines and flaring would be the source of most methane abatement from coal mining, with degasification of surface mines abating a smaller proportion of methane over time. However, research from Kholod et al. (2020) suggested there will be an increase in AMM emissions as coal mines are closed. Methane emissions from AMM are not extensively monitored right now, and there is limited research on the topic. Methane abatement strategies will be needed to abate growing AMM emissions (Zhu et al, 2023). 

In addition, some research suggested CMM is being underestimated, with global emissions being as high as 67 Mt/yr (Assan & Whittle, 2023). If coal demand drops by 90%, as outlined in IEA’s Net Zero Emissions scenario, total coal methane emissions would decline to 3 Mt/yr, and the use of methane abatement would reduce emissions by 2 Mt/yr, leaving only 1 Mt/yr of CMM emitted in 2050. 

With growing interest and investment from governments and academia in identifying methane leaks using technologies such as satellite sensing (MethaneSAT, 2024), the opportunities for methane abatement will increase. Over 150 countries have joined the Global Methane Pledge (representing 50% of the world’s human-caused methane) to reduce methane emissions by 30% of 2020 emissions by 2030 (UNEP, 2021). The IEA (2023a) found that even in a baseline scenario, many governments have announced or put in place measures to cut methane emissions; we would expect a growing trend in global methane abatement to occur. The IEA (2024c) states that in all scenarios global coal demand will decrease. Table 6 shows the statistical low and high achievable ranges for CMM abatement based on different sources for future uptake of CMM abatement.

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Table 6. Range of achievable adoption levels.

Unit: Mt/yr methane abated

Current Adoption 0.59
Achievable – Low 2.83
Achievable – High 4.40
Adoption Ceiling 40.30
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We estimate that the coal industry is currently abating approximately 0.02 Gt CO₂‑eq/yr on a 100-yr basis and 0.03 Gt CO₂‑eq/yr on a 20-yr basis using methane abatement strategies. This is about 1% of total methane emissions emitted in 2024 (IEA, 2025). 

As the coal industry opens or closes coal mines due to changing coal demand, the opportunities for CMM abatement projects will change along with it. If coal demand gradually drops by 2050, more than 0.12 Gt CO₂‑eq/yr of methane could be abated. However, if coal demand drops more quickly from the implementation of energy and climate policies, the methane abatement potential would drop because the coal sector is producing less methane. This is projected in the different energy scenarios modeled by the IEA (2023c). The range between the current CMM abatement and the adoption ceiling is shown in Table 7.

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Table 7. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 0.02
Achievable – Low 0.08
Achievable – High 0.12
Adoption Ceiling 1.12
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Additional Benefits

Food Security 

Methane reacts with chemicals like VOCs to form tropospheric, or ground-level ozone (Fiore et al., 2002). Ground-level ozone has been linked to reduced crop growth and yields (Mills et al., 2018; Samperdo et al., 2023; Tai et al., 2021). Mitigating methane emissions from coal mines could improve food security by reducing ground-level ozone and its harmful impacts on agricultural productivity (Tai et al., 2014; Ramya et al., 2023).

Health and Air Quality

Around 10% of anthropogenic methane comes from coal mines (IEA, 2024a). Methane released from coal mines contributes to ground-level ozone pollution, which can harm lung function, exacerbating conditions like asthma, bronchitis, and emphysema, and can contribute to premature mortality (Mar et al., 2022). Domingo et al. (2024) estimated that ground-level ozone accounted for about 6,600 excess deaths per year in about 400 cities globally. 

Methane released from coal mines also endangers workers’ safety in the mines, increasing the possibility of explosions, which are a significant source of fatalities and injuries (CDC, 2024). In the United States, from 2006 to 2011, mine explosions were responsible for about 25% of fatalities in the mining industry (CDC, 2024). While advances in methane mitigation technologies can prevent explosions and fatalities, mines across LMICs usually do not have methane mitigation protocols in place. Installing methane abatement strategies can potentially protect workers from such explosions (Tate, 2022).

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Risks

CMM abatement strategies could be implemented on a voluntary basis due to favorable natural gas prices, but if natural gas prices drop there is less economic incentive to abate methane (IEA, 2021). Without policy support enforcing methane abatement, emissions could continue, especially from VAM and AMM, which are more difficult to capture and use. Ensuring long-term monitoring and abatement of CMM can be challenging if coal mines are abandoned due to owners going bankrupt, leaving environmental damages unpaid for and remediation up to nearby communities or taxpayers (Ward et al., 2023). 

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Interactions with Other Solutions

Reinforcing

Managing coal methane can have a positive impact on other solutions that reduce methane release to the atmosphere. The use of technologies such as degasification systems, methane destruction, and Leak Detection and Repair (LDAR) in the coal mine sector can demonstrate the effectiveness and economic case for employing methane abatement. This would build momentum for the widespread adoption of methane abatement because successes in the coal sector can be leveraged and applied to other sectors. In addition, LDAR is a key part in identifying where we can abate methane emissions and lessons learned from the coal sector can be applied to other sites, as well as identifying methane leaks in general. 

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Competing

CMM management interacts negatively with solutions that provide clean electricity as this solution captures methane that can be used as an energy source, prolonging the use of natural gas infrastructure and reducing the cost of methane as a fuel source. 

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Dashboard

Solution Basics

Mt methane abated

t CO₂-eq (100-yr)/unit
2.79×10⁷
units/yr
Current 0.59 02.834.4
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.02 0.080.12
US$ per t CO₂-eq
-3
Emergency Brake

CH₄ , N₂O, BC

Trade-offs

Methane abatement strategies are a powerful tool to reduce methane emissions; however, providing a secondary source of revenue for coal mining could increase the profitability and longevity of some coal mines. A broad strategy to reduce reliance on coal as an energy resource is needed to reduce the amount of CMM generated. Even with methane abatement strategies in place, methane used as a fuel or destroyed through flaring will still emit GHGs and contribute to global climate change.

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Mt CO2–eq/yr
< 1
1–3
3–5
5–7
7–9
> 9

Annual emissions from coal mine sources, 2024

Globally, coal mines are responsible for 40 of the 354 Mt of anthropogenic methane emissions in 2024. This is equivalent to 1,116 Mt CO2-eq based on a 100-year GWP time scale. Methane emissions occur throughout the life of a coal mine and can continue after mines are closed or abandoned.

Lewis, C., Tate, R.D., and Mei, D.L. (2024). Fuel operations sector: Coal mining emissions methodology [Data set]. WattTime and Global Energy Monitor, Climate TRACE Emissions Inventory. Retrieved April 18, 2025, from Link to source: https://climatetrace.org

International Energy Agency. (2025). Global methane tracker documentation 2025 version. Link to source: https://iea.blob.core.windows.net/assets/2c0cf2d5-3910-46bc-a271-1367edfed212/GlobalMethaneTracker2025.pdf

Mt CO2–eq/yr
< 1
1–3
3–5
5–7
7–9
> 9

Annual emissions from coal mine sources, 2024

Globally, coal mines are responsible for 40 of the 354 Mt of anthropogenic methane emissions in 2024. This is equivalent to 1,116 Mt CO2-eq based on a 100-year GWP time scale. Methane emissions occur throughout the life of a coal mine and can continue after mines are closed or abandoned.

Lewis, C., Tate, R.D., and Mei, D.L. (2024). Fuel operations sector: Coal mining emissions methodology [Data set]. WattTime and Global Energy Monitor, Climate TRACE Emissions Inventory. Retrieved April 18, 2025, from Link to source: https://climatetrace.org

International Energy Agency. (2025). Global methane tracker documentation 2025 version. Link to source: https://iea.blob.core.windows.net/assets/2c0cf2d5-3910-46bc-a271-1367edfed212/GlobalMethaneTracker2025.pdf

Maps Introduction

Coal mine methane abatement is applicable in any area with coal mines. While China and the United States are the largest coal producers, Russia, Ukraine, Kazakhstan, and India also generated more than 10 Mt CO₂‑eq (100-yr) from coal mines in 2015 (GMI, 2015).

Levels of methane emissions from coal mines can vary geographically. The greatest abatement potential is in China, Kazakhstan, Australia, and several countries in Eastern Europe and Africa (Shindell et al., 2024). However, methane abatement is recommended for all coal mining activities, and high-income countries are in a position to share supportive technologies and practices for coal mine methane abatement with other coal-producing countries to reduce methane emissions from active and abandoned or closed mines.

Action Word
Manage
Solution Title
Coal Mine Methane
Classification
Highly Recommended
Lawmakers and Policymakers
  • Create policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Require all coal mines to measure and report on methane emissions.
  • Invest in monitoring, reporting, and verification technologies, such as satellites, and support low-income countries in monitoring emissions.
  • Provide financial incentives, such as reduced taxes, subsidies, grants, low-interest loans, and feed-in tariffs, for adopting drainage and capture technologies suitable for the region.
  • Require closed and abandoned mines to be sealed and monitored.
  • Compile or update global inventories of the status of abandoned and closed mines.
  • When possible, do not approve the construction of new coal mines.
  • Require low-emitting technologies for equipment, coal processing, storage, and transportation.
  • Develop infrastructure to use captured CMM, including gas processing, grid connections, and industry capacity.
  • Establish clear resource rights to methane emitted from active and abandoned mines.
  • Include CMM recovery in Nationally Determined Contributions and other international reporting instruments.
  • Provide educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Practitioners
  • Utilize or destroy CMM to the maximum extent.
  • Work with policymakers to create policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Measure and report on methane emissions.
  • Invest in monitoring, reporting, and verification technologies, such as satellites, and support low-income countries to monitor emissions.
  • Take advantage of any financial incentives, such as reduced taxes, subsidies, grants, low-interest loans, and feed-in tariffs, to adopt drainage and capture technologies suitable for the region.
  • Ensure abandoned and closed mines are sealed and monitored.
  • Compile or update global inventories of the status of abandoned and closed mines.
  • When possible, do not approve the construction of new coal mines.
  • Develop infrastructure to use captured CMM, including gas processing, grid connections, and industry capacity.
  • Assist policymakers in establishing clear resource rights to methane emitted from active and abandoned mines.
  • Use existing drainage systems for gas capture, utilization, and sale.
  • Improve technologies, such as thermal oxidizers, for the purposes of VAM destruction.
  • Partner with carbon markets that are linked to CMM abatement.
  • Improve CMM emissions modeling and monitoring, including satellites and on-the-ground methods.
  • Invest in R&D to improve extraction, capture, storage, transportation, and utilization technologies.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.
  • Utilize educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.

Further information:

Business Leaders
  • Ensure that operations or investments that include coal mines utilize or destroy methane emissions.
  • Do not invest, plan to use, or create agreements with new coal mines.
  • Invest in high-integrity carbon markets that are linked to CMM abatement.
  • Invest in R&D to improve the efficiency of extraction, capture, storage, transportation, and utilization technologies.
  • Develop infrastructure to use captured CMM, including gas processing, grid connections, and industry capacity.
  • Utilize existing data sets such as the UN’s International Methane Emissions Observatory to inform current and future decisions.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Nonprofit Leaders
  • Advocate for regulating CMM emissions and local policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Assist coal mines in measuring and reporting or conducting independent studies on CMM emissions.
  • Advocate for financial incentives, such as reduced taxes, subsidies, grants, low-interest loans, and feed-in tariffs, for the adoption of drainage and capture technologies suitable for the region.
  • Advocate to stop the construction of new coal mines.
  • Compile or update global inventories of the status of abandoned and closed mines.
  • Help create high-integrity carbon markets that are linked to CMM abatement.
  • Provide educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Investors
  • Invest in monitoring, reporting, and verification technologies, such as satellites, and support low-income countries to monitor emissions.
  • Provide financial support through low-interest loans or green bonds to adopt drainage and capture technologies suitable for the region.
  • Do not invest in constructing new coal mines and require any existing investments to provide transparent emissions data and time-based reduction strategies.
  • Invest in R&D to improve the efficiency of extraction, capture, storage, transportation, and utilization technologies.
  • Develop infrastructure to use captured CMM, including gas processing, grid connections, and industry capacity.
  • Invest in high-integrity carbon markets that are linked to CMM abatement.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Philanthropists and International Aid Agencies
  • Invest in monitoring, reporting, and verification technologies, such as satellites, and support low-income countries to monitor emissions.
  • Provide financial support to adopt drainage and capture technologies suitable for the region.
  • Invest in R&D to improve the efficiency of extraction, capture, storage, transportation, and utilization technologies.
  • Assist in establishing clear resource rights to methane emitted from active and abandoned mines.
  • Help create high-integrity carbon markets that are linked to CMM abatement.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.
  • Provide educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.
  • Advocate for regulating CMM emissions and local policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Compile or update global inventories of the status of abandoned and closed mines.

Further information:

Thought Leaders
  • Advocate for regulating CMM emissions and local policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Assist coal mines in measuring and reporting or conducting independent studies on CMM emissions.
  • Advocate for financial incentives, such as reduced taxes, subsidies, grants, low-interest loans, and feed-in tariffs, for adopting drainage and capture technologies suitable for the region.
  • Assist in establishing clear resource rights to methane emitted from active and abandoned mines.
  • Advocate to stop the construction of new coal mines.
  • Compile or update global inventories of the status of abandoned and closed mines.
  • Help create high-integrity carbon markets that are linked to CMM abatement.
  • Provide educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Technologists and Researchers
  • Improve CMM emissions modeling and monitoring, including satellites and on-the-ground methods.
  • Compile or update global inventories of the status of abandoned and closed mines.
  • Develop infrastructure to use captured CMM, including gas processing, grid connections, and industry capacity.
  • Discover ways to utilize existing drainage systems for gas capture, utilization, and sale.
  • Improve technologies, such as thermal oxidizers, for the purposes of VAM destruction.
  • Develop new ways to improve extraction, capture, storage, transportation, and utilization technologies.
  • Develop verifiable carbon credits using technology such as blockchain to improve the integrity of carbon markets.
  • Improve the efficiency of mining equipment to reduce maintenance requirements and costs.

Further information:

Communities, Households, and Individuals
  • Advocate for regulating CMM emissions and local policies based on global best practices, such as the IEA’s roadmap to implementing CMM regulations.
  • Advocate for financial incentives, such as reduced taxes, subsidies, grants, low-interest loans, and feed-in tariffs, for the adoption of drainage and capture technologies suitable for the region.
  • Advocate to stop the construction of new coal mines.
  • Assist coal mines in measuring and reporting or conducting independent studies on CMM emissions.
  • Provide educational resources to industry leaders, including potential reduction options, workshops, actionable reports, direct engagements, and demonstrations.
  • Join, support, or create public initiatives such as the Global Methane Initiative, Global Methane Pledge, or Global Methane Hub.

Further information:

Sources
Evidence Base

Consensus of effectiveness of abating methane emissions from coal mines: High

There is a high level of consensus about the effectiveness of methane abatement strategies. These strategies can be deployed cost effectively in many cases and have an immediate impact on reducing global temperature rise. 

Authoritative sources such as the IEA (2024c) and UNEP (2021) agree that reducing methane emissions can noticeably slow global climate change. Methane is a short-lived climate pollutant that has a much stronger warming effect than CO₂ over a given time period. IEA (2023d) identified that close to 55% (22 Mt) of CMM emissions could be abated with existing technologies. However, there are significant challenges in measuring and recovering methane emissions in the coal sector. Analysis from Assan & Whittle (2023) found that global CMM emissions could be significantly higher than reported, 38–67 Mt/yr compared with the 40 Mt/yr reported by the IEA (2025).

The IEA (2023a) noted that more than half of CMM emissions could be abated through utilization, flaring, or oxidation technologies, with abatement being more practical for underground mines. Many studies (DeFabrizio et al., 2021; Malley et al., 2023; Shindell et al., 2024) have shown that methane abatement strategies can use existing technologies, often at low cost. In some countries, coal operators already identify the location and sources of CMM to meet health and safety regulations (Assan & Whittle, 2023); Setiawan & Wright (2024) noted that existing technologies such as pre-mine drainage and VAM mitigation have been proven in various places around the world over the past 25 years. According to UNEP (2021), coal methane abatement could reduce emissions by 12–25 Mt/yr, with up to 98% of the measures implemented at low cost. However, costs may vary significantly based on the available infrastructure and characteristics of an individual coal mine.

The results presented in this document summarize findings from 21 reviews and meta-analyses and 20 original studies reflecting current evidence from three countries (Australia, China, and the United States) as well as from sources examining global CMM emissions. We recognize this limited geographic scope creates bias, and hope this work inspires research and data sharing on this topic in underrepresented regions.

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Appendix

CMM abatement strategy constraints:

The type of coal mine, the amount of methane produced, and the available infrastructure greatly affect which abatement strategies are economical. Underground coal mines often produce more CMM and are likely to capture CMM using degasification systems and use it for productive purposes such as electricity generation or selling captured methane. However, VAM, which is a major part of CMM emissions, can be challenging to use for productive purposes due to the low methane concentrations. VAM requires regenerative thermal oxidation technology to effectively destroy and with more gassy coal mines. According to the IEA (2023b), technologies such as flaring and drained CMM can be used at less gassy mines with lower initial capital cost. Capturing methane for destruction has the disadvantage of not creating a source of revenue to offset the capital cost of methane abatement without a form of carbon markets in place. 

More than 60% of methane-related emissions from coal mining are from the ventilation of underground coal mines. Large amounts of fresh air are used to lower the concentration of methane and reduce the risk of explosions in underground mines. This makes it challenging to destroy or use the low concentrations of VAM (UNEP, 2022). It is also challenging to capture methane from surface mines because the coal is in direct contact with the atmosphere and over a larger surface area. However, thermal oxidation systems have been used to destroy VAM (U.S. EPA, 2019) and there have been examples of degasification systems used for surface mines as well (IEA, 2023b). Methane emissions from AMM can be dealt with by flooding underground mines with water (Kholod et al., 2020) or by sealing and using capture and utilization projects (Zhu et al., 2023). 

Technologies for reducing methane emissions can be divided between underground and surface coal mines:

Underground mines
  • Predainage prior to mining
  • VAM capture and utilization
  • Capture of abandoned mine gas
  • Sealing or flooding of abandoned mines 
Surface mines
  • Degasification of surface mines
  • Predrainage of surface mines

Appendix References

CNX. (2024, March 20). Jumpstarting coal mine methane capture projects for beneficial end use [PowerPoint slides].Global Methane Initiative. https://www.globalmethane.org/resources/details.aspx?resourceid=5386 

United Nations Economic Commission for Europe (UNECE). (2019). Best practice guidance for effective methane recovery and use from abandoned coal mines. https://unece.org/fileadmin/DAM/energy/images/CMM/CMM_CE/Best_Practice_Guidance_for_Effective_Methane_Recovery_and_Use_from_Abandoned_Coal_Mines_FINAL__with_covers_.pdf 

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Updated Date

Mobilize Electric Cars

Submitted by Drawdown Admin on
Sector
Transportation
Mode
Cut Emissions
Cluster
Electrify Vehicles Fuel Switching
Image
Electric car plugged into charging station
Coming Soon
Off
Summary

Electric cars are four-wheeled passenger cars that run on electricity, usually from the electricity grid and stored in onboard batteries (i.e., not including fuel cell electric cars). This definition includes electric pickup trucks, motorhomes, and other such vehicles. It does not include two-wheeled vehicles or hybrid cars (which combine an electric motor with a gasoline or diesel engine). It also does not include freight and commercial vehicles, such as electric heavy trucks, buses, and ambulances. We define Mobilizing Electric Cars as replacing fossil fuel–powered cars (i.e., those powered by internal combustion engines) with electric equivalents, as well as building out the necessary infrastructure (especially charging stations) to support them.

Income & work,Health
Water quality,Air quality
Description for Social and Search
Mobilize Electric Cars is a Highly Recommended climate solution. Electric cars slash air pollution and greenhouse gases, especially when powered by clean grids.
Overview

Electric cars provide the same functionality as fossil fuel–powered cars, but use electric motors rather than fuel-burning engines. The energy for the motors comes from an onboard battery, which is normally charged using electricity from the grid.

Electric cars have no direct tailpipe emissions, since electric motors do not burn fuel to function. The grid electricity used to charge their batteries may have come from fossil fuel-burning power plants, meaning electric cars are not entirely free of direct emissions. However, in most electrical grids, even those that mainly generate electricity from fossil fuels, electric cars usually still produce fewer emissions per pkm than fossil fuel–powered cars. This is for three reasons. First, large, fixed power plants and efficient electric grids can convert fossil fuels into useful energy more efficiently than smaller, mobile internal combustion engines in cars. In extreme cases, such as grids powered entirely by coal, this might not be the case, particularly if the grid has a lot of transmission and distribution losses. Second, the powertrain of an electric car delivers electricity from the battery to the wheels much more efficiently than the powertrain of a fossil fuel–powered car, which wastes much more energy as heat (International Transport Forum, 2020; Mofolasayo, 2023; Verma et al., 2022). Third, electric cars’ powertrains enable regenerative braking, where the kinetic energy of the car’s motion is put back into the battery when the driver brakes (Yang et al., 2024).

Electric cars reduce emissions of CO₂,  methane, and nitrous oxide to the atmosphere by replacing fuel-powered cars, which emit these gases from their tailpipes.

APEC. (2024). Connecting Traveler Choice with Climate Outcomes: Innovative Greenhouse Gas Emissions Reduction Policies and Practices in the APEC Region through Traveler Behavioral Change. Link to source: https://www.apec.org/publications/2024/09/connecting-traveler-choice-with-climate-outcomes--innovative-greenhouse-gas-emissions-reduction-policies-and-practices-in-the-apec-region-through-traveler-behavioral-change 

Agusdinata, D. B., Liu, W., Eakin, H., & Romero, H. (2018). Socio-environmental impacts of lithium mineral extraction: Towards a research agenda. Environmental Research Letters, 13(12). Scopus. Link to source: https://doi.org/10.1088/1748-9326/aae9b1

Anenberg, S. C., Miller, J., Henze, D., & Minjares, R. (2019, February 26). A global snapshot of the air pollution-related health impacts of transportation sector emissions in 2010 and 2015. International Council on Clean Transportation. Link to source: https://theicct.org/publication/a-global-snapshot-of-the-air-pollution-related-health-impacts-of-transportation-sector-emissions-in-2010-and-2015/

Bloomberg New Energy Finance. (2024). Electric Vehicle Outlook 2024. Bloomberg. Link to source: https://about.bnef.com/electric-vehicle-outlook/

Carey, J. (2023). The other benefit of electric vehicles. Proceedings of the National Academy of Sciences, 120(3), e2220923120. Link to source: https://doi.org/10.1073/pnas.2220923120

Castelvecchi, D. (2021). Electric cars and batteries: How will the world produce enough? Nature, 596(7872), 336–339. Link to source: https://doi.org/10.1038/d41586-021-02222-1

Choma, E. F., Evans, J. S., Hammitt, J. K., Gómez-Ibáñez, J. A., & Spengler, J. D. (2020). Assessing the health impacts of electric vehicles through air pollution in the United States. Environment International, 144, 106015. Link to source: https://doi.org/10.1016/j.envint.2020.106015

Dillman, K. J., Árnadóttir, Á., Heinonen, J., Czepkiewicz, M., & Davíðsdóttir, B. (2020). Review and Meta-Analysis of EVs: Embodied Emissions and Environmental Breakeven. Sustainability, 12(22), Article 22. Link to source: https://doi.org/10.3390/su12229390

Electric vehicle database. (2024). Energy consumption of full electric vehicles. Electric Vehicle Database. Link to source: https://ev-database.org/cheatsheet/energy-consumption-electric-car

Fakhrooeian, P., Pitz, V., & Scheppat, B. (2024). Systematic Evaluation of Possible Maximum Loads Caused by Electric Vehicle Charging and Heat Pumps and Their Effects on Common Structures of German Low-Voltage Grids. World Electric Vehicle Journal, 15(2), 49. Link to source: https://doi.org/10.3390/wevj15020049

Garcia, E., Johnston, J., McConnell, R., Palinkas, L., & Eckel, S. P. (2023). California’s early transition to electric vehicles: Observed health and air quality co-benefits. The Science of the Total Environment, 867, 161761. Link to source: https://doi.org/10.1016/j.scitotenv.2023.161761

Goetzel, N., & Hasanuzzaman, M. (2022). An empirical analysis of electric vehicle cost trends: A case study in Germany. Research in Transportation Business & Management, 43, 100825. Link to source: https://doi.org/10.1016/j.rtbm.2022.100825

Guarnieri, M., & Balmes, J. R. (2014). Outdoor air pollution and asthma. Lancet, 383(9928), 1581–1592. Link to source: https://doi.org/10.1016/S0140-6736(14)60617-6

IEA. (2022). Electric Vehicles: Total Cost of Ownership Tool. IEA. Link to source: https://www.iea.org/data-and-statistics/data-tools/electric-vehicles-total-cost-of-ownership-tool

IEA. (2024). Global EV Outlook 2024. International Energy Agency. Link to source: https://www.iea.org/reports/global-ev-outlook-2024

International Council on Clean Transportation. (2024). Clearing the air: Why EVs can outperform conventional vehicles in freezing temperatures. International Council on Clean Transportation. Link to source: https://theicct.org/clearing-the-air-why-evs-can-outperform-conventional-vehicles-in-freezing-temperatures-oct24/

International Transport Forum. (2020). Good to Go? Assessing the Environmental Performance of New Mobility (Corporate Partnership Board). OECD. Link to source: https://www.itf-oecd.org/sites/default/files/docs/environmental-performance-new-mobility.pdf

IPCC. (2022). Mitigation of Climate Change. Contribution of Working Group III to the Sixth Assessment Report of the Intergovernmental Panel on Climate Change. Cambridge. Link to source: https://www.ipcc.ch/report/ar6/wg3/downloads/report/IPCC_AR6_WGIII_FullReport.pdf

Jones, S. J. (2019). If electric cars are the answer, what was the question? British Medical Bulletin, 129(1), 13–23. Link to source: https://doi.org/10.1093/bmb/ldy044

Kerr, G. H., Goldberg, D. L., & Anenberg, S. C. (2021). COVID-19 pandemic reveals persistent disparities in nitrogen dioxide pollution. Proceedings of the National Academy of Sciences, 118(30), e2022409118. Link to source: https://doi.org/10.1073/pnas.2022409118

Kittner, N., Tsiropoulos, I., Tarvydas, D., Schmidt, O., Staffell, I., & Kammen, D. M. (2020). Chapter 9—Electric vehicles. In M. Junginger & A. Louwen (Eds.), Technological Learning in the Transition to a Low-Carbon Energy System (pp. 145–163). Academic Press. Link to source: https://doi.org/10.1016/B978-0-12-818762-3.00009-1

Larson, E., Grieg, C., Jenkins, J., Mayfield, E., Pascale, A., Zhang, C., Drossman, J., Williams, R., Pacala, S., Socolow, R., Baik, E., Birdesy, R., Duke, R., Jones, R., Haley, B., Leslie, E., Paustain, K., & Swan, A. (2021). Net-Zero America: Potential Pathways, Infrastructure, and Impacts. Princeton University. Link to source: https://lpdd.org/resources/princeton-report-net-zero-america/

Melaina, M., Bush, B., Eichman, J., Wood, E., Stright, D., Krishnan, V., Keyser, D., Mai, T., & McLaren, J. (2016). National Economic Value Assessment of Plug-in Electric Vehicles: Volume I (No. NREL/TP-5400-66980). National Renewable Energy Lab. (NREL), Golden, CO (United States). Link to source: https://doi.org/10.2172/1338175

Milovanoff, A., Posen, I. D., & MacLean, H. L. (2020). Electrification of light-duty vehicle fleet alone will not meet mitigation targets. Nature Climate Change, 1–6. Link to source: https://doi.org/10.1038/s41558-020-00921-7

Mofolasayo, A. (2023). Assessing and Managing the Direct and Indirect Emissions from Electric and Fossil-Powered Vehicles. Sustainability, 15(2), Article 2. Link to source: https://doi.org/10.3390/su15021138

Nguyen, C. T. P., Nguyễn, B.-H., Ta, M. C., & Trovão, J. P. F. (2023). Dual-Motor Dual-Source High Performance EV: A Comprehensive Review. Energies, 16(20), Article 20. Link to source: https://doi.org/10.3390/en16207048

Nickel Institute. (2021a). Asia Pacific and UK Automotive ICE vs EV Total Cost of Ownership. Link to source: https://nickelinstitute.org/media/8d993d1b8165b23/tco-asia-pacific-automotive.pdf

Nickel Institute. (2021b). European Union and UK Automotive ICE vs EV Total Cost of Ownership. Link to source: https://nickelinstitute.org/media/8d9058c08d2bcf2/avicenne-study-tco-eu-and-uk-automotive.pdf

Nickel Institute. (2021c). North American Automotive ICE vs EV Total Cost of Ownership. Link to source: https://nickelinstitute.org/media/8d993d0fd3dfd5b/tco-north-american-automotive-final.pdf

Pan, S., Yu, W., Fulton, L. M., Jung, J., Choi, Y., & Gao, H. O. (2023). Impacts of the large-scale use of passenger electric vehicles on public health in 30 US. metropolitan areas. Renewable and Sustainable Energy Reviews, 173, 113100. Link to source: https://doi.org/10.1016/j.rser.2022.113100

Pennington, A. F., Cornwell, C. R., Sircar, K. D., & Mirabelli, M. C. (2024). Electric vehicles and health: A scoping review. Environmental Research, 251, 118697. Link to source: https://doi.org/10.1016/j.envres.2024.118697

Peters, D. R., Schnell, J. L., Kinney, P. L., Naik, V., & Horton, D. E. (2020). Public health and climate benefits and trade‐offs of U.S. vehicle electrification. GeoHealth, 4, e2020GH000275. Link to source: https://doi.org/10.1029/2020GH000275 

Ravi, S. S., & Aziz, M. (2022). Utilization of Electric Vehicles for Vehicle-to-Grid Services: Progress and Perspectives. Energies, 15(2), Article 2. Link to source: https://doi.org/10.3390/en15020589

Ren, Y., Sun, X., Wolfram, P., Zhao, S., Tang, X., Kang, Y., Zhao, D., & Zheng, X. (2023). Hidden delays of climate mitigation benefits in the race for electric vehicle deployment. Nature Communications, 14(1), 3164. Link to source: https://doi.org/10.1038/s41467-023-38182-5

Requia, W. J., Mohamed, M., Higgins, C. D., Arain, A., & Ferguson, M. (2018). How clean are electric vehicles? Evidence-based review of the effects of electric mobility on air pollutants, greenhouse gas emissions and human health. Atmospheric Environment, 185, 64–77. Link to source: https://doi.org/10.1016/j.atmosenv.2018.04.040

Roberts, C. (2022). Easy Street for Low-Carbon Mobility? The Political Economy of Mass Electric Car Adoption. In G. Parkhurst & W. Clayton (Eds.), Electrifying Mobility: Realising a Sustainable Future for the Car (Vol. 15, pp. 13–31). Emerald Publishing Limited. Link to source: https://doi.org/10.1108/S2044-994120220000015004

Sovacool, B. K. (2019). The precarious political economy of cobalt: Balancing prosperity, poverty, and brutality in artisanal and industrial mining in the Democratic Republic of the Congo. The Extractive Industries and Society, 6(3), 915–939. Link to source: https://doi.org/10.1016/j.exis.2019.05.018

Szyszkowicz, M., Kousha, T., Castner, J., & Dales, R. (2018). Air pollution and emergency department visits for respiratory diseases: A multi-city case crossover study. Environmental Research, 163, 263–269. Link to source: https://doi.org/10.1016/j.envres.2018.01.043

Vega-Perkins, J., Newell, J. P., & Keoleian, G. (2023). Mapping electric vehicle impacts: Greenhouse gas emissions, fuel costs, and energy justice in the United States. Environmental Research Letters, 18(1), 014027. Link to source: https://doi.org/10.1088/1748-9326/aca4e6

Verma, S., Dwivedi, G., & Verma, P. (2022). Life cycle assessment of electric vehicles in comparison to combustion engine vehicles: A review. Materials Today: Proceedings, 49, 217–222. Link to source: https://doi.org/10.1016/j.matpr.2021.01.666

Weiss, M., Dekker, P., Moro, A., Scholz, H., & Patel, M. K. (2015). On the electrification of road transportation – A review of the environmental, economic, and social performance of electric two-wheelers. Transportation Research Part D: Transport and Environment, 41, 348–366. Link to source: https://doi.org/10.1016/j.trd.2015.09.007

WHO. (2024). Number of registered vehicles. Link to source: https://www.who.int/data/gho/data/indicators/indicator-details/GHO/number-of-registered-vehicles

Yang, C., Sun, T., Wang, W., Li, Y., Zhang, Y., & Zha, M. (2024). Regenerative braking system development and perspectives for electric vehicles: An overview. Renewable and Sustainable Energy Reviews, 198, 114389. Link to source: https://doi.org/10.1016/j.rser.2024.114389

Yoder, K. (2023, June 14). The environmental disaster lurking beneath your neighborhood gas station. Grist. Link to source: https://grist.org/accountability/gas-stations-underground-storage-tank-leaks-environmental-disaster/

Credits

Lead Fellow

  • Cameron Roberts, Ph.D.

Contributors

  • Ruthie Burrows, Ph.D.

  • James Gerber, Ph.D.

  • Daniel Jasper

  • Heather Jones, Ph.D.

  • Heather McDiarmid, Ph.D.

  • Alex Sweeney

Internal Reviewers

  • Aiyana Bodi

  • James Gerber, Ph.D.

  • Hannah Henkin

  • Jason Lam

  • Ted Otte

  • Amanda D. Smith, Ph.D.
Effectiveness

Every million pkm shifted from fossil fuel–powered cars to electric cars reduces 48.52 t CO₂‑eq on a 100-yr basis (Table 1), or 49.13 t CO₂‑eq on a 20-yr basis. 

We found this by collecting data on electricity consumption for a range of electric car models (Electric Vehicle Database, 2024) and multiplying it by the global average emissions per kWh of electricity generation. Fossil fuel–powered cars emit 115.3 t CO₂‑eq/million pkm on a 100-yr basis (116.4 t CO₂‑eq/million pkm on a 20-yr basis). Electric cars already have lower emissions in countries with large shares of renewable, nuclear, or hydropower generation in their electricity grids (International Transport Forum, 2020; Verma et al., 2022).

These data come disproportionately from North America and Europe, and, notably, leave out China, which has made major progress on electric cars in recent years and has many of its own makes and models. 

Electric cars today are disproportionately used in high- and upper-middle-income countries, whose electricity grids emit fewer GHG emissions than the global average per unit of electricity generated (IEA, 2024). Electric cars in use today reduce more emissions on average than the figure we have calculated. 

Electric cars have higher embodied emissions than fossil fuel–powered cars, due to the GHG-intensive process of manufacturing batteries. This gives them a carbon payback period which ranges from zero to over 10 years (Dillman et al., 2020; Ren et al., 2023).

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Table 1. Effectiveness at reducing emissions.

Unit: t CO₂‑eq/million pkm, 100-yr basis

25th percentile 38.95
mean 49.54
median (50th percentile) 48.52
75th percentile 62.82

Shifted from fossil fuel–powered cars to electric cars, 100-yr basis.

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Cost

Including purchase price, financing, fuel and electricity costs, maintenance costs, and insurance, electric cars cost on average US$0.05 less per pkm (US$49,442.19/million pkm) than fuel-powered cars. This is based on a population-weighted average of the cost differential between electric and fossil fuel–powered cars in seven countries: Japan, South Korea, China, the United States, France, Germany, and the United Kingdom (Nickel Institute, 2021b, 2021c, 2021a). 

While this analysis found that electric cars are less expensive than fossil fuel–powered cars almost everywhere, the margin is often quite small. The difference is less than US$0.01/pkm (US$10,000/million pkm) in South Korea, the United States, and Germany. In some markets, electric cars are more expensive per pkm than fossil fuel–powered cars (IEA, 2022).

This amounts to savings of US$1,019/t CO₂‑eq on a 100-yr basis (Table 2), or US$1,006/t CO₂‑eq avoided emissions on a 20-yr basis). 

Our analysis does not include costs that are the same for both electric and fossil fuel–powered cars, including taxes, insurance costs, and public costs of building road infrastructure.

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Table 2. Cost per unit climate impact.

Unit: 2023 US$/t CO₂‑eq, 100-yr basis

median -1,019
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Learning Curve

For every doubling in electric car production, costs decline by approximately 23% (Table 3; Goetzel & Hasanuzzaman, 2022; Kittner et al., 2020; Weiss et al., 2015). 

In addition to manufacturing improvements and economies of scale, this reflects rapid technological advancements in battery production, which is a significant cost component of an electric powertrain (Weiss et al., 2015).

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Table 3. Learning rate: drop in cost per doubling of the installed solution base.

Unit: %

25th percentile 23.00
mean 22.84
median (50th percentile) 23.00
75th percentile 24.00
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Speed of Action

Speed of action refers to how quickly a climate solution physically affects the atmosphere after it is deployed. This is different from speed of deployment, which is the pace at which solutions are adopted.

At Project Drawdown, we define the speed of action for each climate solution as emergency brake, gradual, or delayed.

Mobilize Electric Cars is a GRADUAL climate solution. It has a steady, linear impact on the atmosphere. The cumulative effect over time builds as a straight line.

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Caveats

The effectiveness of electric cars in mitigating GHG emissions is critically dependent on the emissions associated with electricity production. In electricity grids dominated by fossil fuels, electric cars have far higher emissions than in jurisdictions with low-emission electricity generation (International Transport Forum, 2020; IPCC, 2022; Milovanoff et al., 2020).

Electric car adoption faces a major obstacle in the form of constraints on battery production. While electric car battery production is being aggressively upscaled (IEA, 2024), building enough batteries to replace a significant fraction of fossil fuel–powered cars is an enormous challenge and will likely slow down a transition to electric cars, even if there is very high consumer demand (Milovanoff et al., 2020). 

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Current Adoption

Approximately 28 million electric cars are in use worldwide (IEA, 2024). This corresponds to about 819,000 million pkm traveled by electric car worldwide each year (Table 4). We assume that all of this travel would be undertaken by a fossil fuel–powered car if the car’s occupants did not use an electric car. Adoption is much higher in some countries, such as Norway, where the share of electric cars was 29% in 2023.

To convert the IEA’s electric car estimates into pkm traveled, we needed to determine the average passenger-distance that each passenger car travels per year. Using population-weighted data from several different countries, the average car carries 1.5 people and travels an average of 29,250 pkm/yr. Multiplying this number by the number of electric cars in use gives the total travel distance shift from fossil fuel–powered cars to electric cars.

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Table 4. Current (2024) adoption level.

Unit: million pkm/yr

Population-weighted mean 818,900

Implied travel shift from fossil fuel-powered cars to electric cars.

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Adoption Trend

Globally, about 104 billion pkm are displaced from fossil fuel–powered cars by electric cars every year (Table 5). The number of new electric cars purchased each year is growing at an average rate of over 10% (Bloomberg New Energy Finance, 2024; IEA, 2024), although purchase rates have declined slightly from record highs between 2020–2022. Global purchases of electric cars are still increasing by around 3.6 million cars/yr. This is based on globally representative data (Bloomberg New Energy Finance, 2024; IEA, 2024).

Despite this impressive rate of growth, electric cars still have a long way to go before they replace a large percentage of the more than 2 billion cars currently driven (WHO, 2024).

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Table 5. 2023-2024 adoption trend.

Unit: million pkm/yr

Median, or population-weighted mean 104,000

Implied travel shift from fossil fuel-powered cars to electric cars.

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Adoption Ceiling

The adoption ceiling for electric cars is equal to the total passenger-distance driven by the more than 2 billion cars worldwide (WHO, 2024). Using a population-weighted mean of the average distance (in pkm) traveled per car annually, this translates to about 59 trillion pkm (Table 6).

Replacing every single fossil fuel–powered car with an electric car would require an enormous upscaling of electric car production capacity, rapid development of charging infrastructure, cost reductions to increase affordability, and technological improvements to improve suitability for more kinds of drivers and trips. It would also face cultural obstacles from drivers who are attached to fossil fuel–powered cars (Roberts, 2022).

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Table 6. Adoption ceiling.

Unit: million pkm/yr

Median, or population-weighted mean 59,140,000

Implied travel shift from fossil fuel-powered cars to electric cars.

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Achievable Adoption

The achievable adoption of electric car travel ranges from about 26–47 trillion pkm displaced from fossil fuel–powered cars (Table 7).

Various organizations have produced forecasts for electric car adoption. These are not assessments of feasible adoption per se; they are instead trying to predict likely rates of adoption, given various assumptions about the future (Bloomberg New Energy Finance, 2024; IEA, 2024). However, they are useful in that they take a large number of different variables into account to make their estimates. To convert these estimates of future likely adoption into estimates of the achievable adoption range, we apply some assumptions to the numbers in the scenario projections. 

To find a high rate of electric car adoption, we assume that every country could reach the highest rate of adoption projected to occur for any country. Bloomberg New Energy Finance’s (2024) Economic Transition scenario predicts that Norway will reach an 80% electric vehicle stock share by 2040. We therefore set our high adoption rate at 80% worldwide. This corresponds to 1,617 million total electric cars in use, or 47 trillion pkm traveled by electric car. An important caveat is that with a global supply constraint in the production of electric car batteries, per-country adoption rates are somewhat zero-sum. Every electric car purchased in Norway is one that cannot be purchased elsewhere. Therefore, for the whole world to achieve an 80% electric car stock share, global electric car and battery production would have to increase radically. While this might be possible due to technological improvements or radical increases in investment, it should not be taken for granted.

To identify a lower feasible rate of electric car adoption, we simply take the highest estimate for global electric car adoption. Bloomberg’s Economic Transition scenario predicts 44% global electric car adoption by 2050. This corresponds to 890 million electric cars, or 26 trillion pkm.

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Table 7. Range of achievable adoption levels.

Unit: million pkm/yr

Current Adoption 818,900
Achievable – Low 26020000
Achievable – High 47310000
Adoption ceiling (physical limit) 59140000
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Electric cars are currently displacing 0.040 Gt CO₂‑eq of GHG emissions from the transportation system on a 20-yr basis (Table 8), or 0.040 Gt CO₂‑eq on a 100-yr basis. 

If electric cars reach 44% of the global car stock share by 2040, as Bloomberg (2024) projects, without any change in the total number of cars on the road, they will displace 1.263 Gt CO₂‑eq GHG emissions on a 100-yr basis (1.279 Gt CO₂‑eq  on a 20-yr basis).

If electric cars globally reach 80% of car stock share, as Bloomberg projects might happen in Norway by 2040, they will displace 2.296 Gt CO₂‑eq GHG emissions on a 100-yr basis (2.325 Gt CO₂‑eq on a 20-yr basis).

If electric cars replace 100% of the global car fleet, they will displace 2.870 Gt CO₂‑eq  GHG emissions on a 100-yr basis (2.906 Gt CO₂‑eq on a 20-yr basis).

These numbers are based on the present-day average emissions intensity from electrical grids in countries with high rates of electric car adoption. If more clean energy is deployed on electricity grids, the total climate impact from electric cars will increase considerably.

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Table 8. Climate impact at different levels of adoption.

Unit: Gt CO₂‑eq/yr, 100-yr basis

Current Adoption 0.040
Achievable – Low 1.263
Achievable – High 2.296
Adoption ceiling (physical limit) 2.870
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Additional Benefits

Health

Since electric cars do not have tailpipe emissions, they can mitigate traffic-related air pollution, which is associated with asthma, lung cancer, increased emergency department visits for respiratory disease, and increased mortality (Anenberg et al., 2019; Guarnieri & Balmes, 2014; Pan et al., 2023; Pennington et al., 2024; Requia et al., 2018; Szyszkowicz et al., 2018). Transitioning to electric cars can reduce exposure to air pollution, improve health, and prevent premature mortality (Garcia et al., 2023; Larson et al., 2021; Peters et al., 2020).

The health benefits of adopting electric cars vary spatially and partly depend upon how communities generate electricity (Choma et al., 2020), but there is evidence that they have improved health. A study in California found a reduction in emergency department visits in ZIP codes with an increase in zero-emissions cars (Garcia et al., 2023). By 2050, projections estimate that about 64,000–167,000 deaths could be avoided by adopting electric cars (Larson et al., 2021).

Communities rich in racial and ethnic minorities tend to be located near highways and major traffic corridors and so are disproportionately exposed to air pollution (Kerr et al., 2021). Transitioning to electric cars could improve health in marginalized urban neighborhoods that are located near highways, industry, or ports (Pennington et al., 2024). These benefits depend upon an equitable distribution of electric cars and infrastructure to support the adoption of electric cars (Garcia et al., 2023). Low-income households may not see the same savings from an electric car due to the cost and stability of electricity prices and distance to essential services (Vega-Perkins et al., 2023)

Income and Work

Adopting electric cars can reduce a household’s energy burden, or the proportion of income spent on residential energy (Vega-Perkins et al., 2023). About 90% of United States households that use a car could see a reduction in energy burden by transitioning to an electric car. Money spent to charge electric cars is more likely to stay closer to the local community where electricity is generated, whereas money spent on fossil fuels often benefits oil-producing regions. This benefits local and national economies by improving their trade balance (Melaina et al., 2016).

Water Quality

Substituting electric car charging points for gas stations can eliminate soil and water pollution from leaking underground gas tanks (Yoder, 2023). 

Air Quality

The adoption of electric cars reduces emissions of air pollutants, including sulfur oxides, sulfur dioxide, and nitrous oxides, and especially carbon monoxide and volatile organic compounds. It has a smaller impact on particulate emissions (Requia et al., 2018). Some air pollution reductions are limited (particularly PM and ozone) due to heavier electric cars and pollution from brakes, tires, and wear on the batteries (Carey, 2023; Jones, 2019).

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Risks

Mining minerals necessary to produce electric car batteries carries environmental and social risks. This has been associated with significant harms, particularly in lower-income countries that supply many of these minerals (Agusdinata et al., 2018; Sovacool, 2019).

Electric cars might also pose added safety risks due to their higher weight, which means they have longer stopping distances and can cause more significant damage in collisions and to pedestrians and cyclists (Jones, 2019). This risk includes dual-motor electric cars that incorporate two electric motors – one for the front axle and one for the rear – providing all-wheel drive (AWD) capabilities. The addition of a second motor increases the vehicle's weight and complexity, which can lead to higher energy consumption and reduced overall efficiency. Moreover, the increased manufacturing costs associated with dual-motor systems can result in higher purchase prices for consumers (Nguyen et al., 2023). However, this configuration enhances vehicle performance, offering improved acceleration, traction, and handling, particularly in adverse weather conditions, which are valued by some consumers. 

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Interactions with Other Solutions

Reinforcing

Electric car batteries can potentially be used as stationary batteries for use as energy storage to balance electrical grids, either through vehicle-to-grid (V2G) technology or with degraded electric car batteries being installed in stationary battery farms as a form of reuse (Ravi & Aziz, 2022). 

The effectiveness of electric cars in reducing GHG emissions increases as electricity grids become cleaner, since lower-carbon electricity further reduces the emissions associated with car charging. 

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Competing

Electric cars compete with heat pumps for electricity. Installing both heat pumps and electric cars could strain the electric grid’s capacity (Fakhrooeian et al., 2024).

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Scaling up the production of electric cars requires more mining of critical minerals, which could affect ecosystems that are valuable carbon sinks (Agusdinata et al., 2018).

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Getting travelers onto bicycles, sidewalks, public transit networks, or smaller electric vehicles (such as electric bicycles) provides a greater climate benefit than getting them into electric cars. There is an opportunity cost to deploying electric cars because those resources could otherwise be used to support these more effective solutions (APEC, 2024).

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Dashboard

Solution Basics

million passenger-kilometers (million pkm)

t CO₂-eq (100-yr)/unit
038.9548.52
units/yr
Current 818,900 02.602×10⁷4.731×10⁷
Achievable (Low to High)

Climate Impact

Gt CO₂-eq (100-yr)/yr
Current 0.04 1.2632.296
US$ per t CO₂-eq
-1,019
Gradual

CO₂, CH₄, N₂O, BC

Trade-offs

Electric car batteries are currently quite emissions-intensive to produce, resulting in high embodied emissions. While the embodied emissions are higher for electric cars than fossil fuel–powered cars, the results are mixed when coupling these with operating emissions. Dillman et al.’s (2020) review of the literature on this topic found that producing the average battery-electric car emits 63% more GHG emissions than the average gasoline-powered car, and 77% more GHG emissions than the average diesel-powered car. Taking their lower tailpipe emissions into account, this gives them a GHG payback period of zero to more than 10 years. In some cases, the emissions payback period is longer than the expected lifespan of the electric car, meaning it will have higher life cycle GHG emissions than a comparable gasoline or diesel-powered car. However, the ITF (2020) found that the lifetime emissions from manufacturing, operation, and infrastructure are lower for electric cars. All of these studies relied on assumptions, including the type of car, size of battery, electricity grid, km/yr, and lifetime. 

There is some criticism against any solution that advocates for car ownership, contending that the focus should be on solutions such as Enhance Public Transit that reduce car ownership and usage. Jones (2019) noted “there is little evidence to suggest that EVs can offer the universal solution that global governments are seeking,” and that efforts to popularize electric cars “may be better directed at creating more efficient public transport systems, rather than supporting personal transportation, if the significant health disbenefits of car use during the past 150 years are to be in any way reduced.”

Milovanoff et al. (2020) offered similar criticism: “Closing the mitigation gap solely with EVs would require more than 350 million on-road EVs (90% of the fleet), half of national electricity demand, and excessive amounts of critical materials to be deployed in 2050. Improving [the] average fuel consumption of fossil fuel–powered vehicles, with stringent standards and weight control, would reduce the requirement for alternative technologies, but is unlikely to fully bridge the mitigation gap. There is therefore a need for a wide range of policies that include measures to reduce vehicle ownership and usage.”

Allocating the limited global battery supply to privately owned electric cars might undermine the deployment of other solutions that also require batteries, but are more effective at avoiding GHG emissions (Castelvecchi, 2021). These could include electric buses, electric rail, and electric bicycles.

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Mt CO2-eq
0–4
4–8
8–12
12–16
16–20
> 20
No data

Annual road transportation emissions, 2024

Cars are the largest source of vehicle emissions, which are shown here for urban areas.

Kott, T., Foster, K., Villafane-Delgado, M., Loschen, W., Sicurello, P., Ghebreselassie, M., Reilly, E., and Hughes, M. (2024). Transportation sector - Global road emissions. [Data set]. The Johns Hopkins University Applied Physics Laboratory (JHU/APL), Climate TRACE Emissions Inventory. Retrieved March 12, 2025 from Link to source: https://climatetrace.org

Mt CO2-eq
0–4
4–8
8–12
12–16
16–20
> 20
No data

Annual road transportation emissions, 2024

Cars are the largest source of vehicle emissions, which are shown here for urban areas.

Kott, T., Foster, K., Villafane-Delgado, M., Loschen, W., Sicurello, P., Ghebreselassie, M., Reilly, E., and Hughes, M. (2024). Transportation sector - Global road emissions. [Data set]. The Johns Hopkins University Applied Physics Laboratory (JHU/APL), Climate TRACE Emissions Inventory. Retrieved March 12, 2025 from Link to source: https://climatetrace.org

Maps Introduction

Electric cars can effectively mitigate climate change in all geographic regions, although there is spatial variability that influences per-pkm effectiveness and potential solution uptake. Effectiveness heavily depends on the carbon intensity of the charging source, which varies greatly between and within countries. The effectiveness of electric cars decreases for larger vehicles, favored in some countries (Jones, 2019; Nguyen et al., 2023).  

The uptake of electric cars can be significantly influenced by socioeconomic factors, including the relative costs of fuels and electricity, the capacity of civil society to provide adequate charging infrastructure, and the availability of subsidies for electric vehicles.

Extreme temperatures can negatively impact vehicle range, both by slowing battery chemistry and increasing energy demands for regulating passenger compartment temperature, which can adversely affect consumers’ perceptions of electric car suitability in locations with such climates (International Council on Clean Transportation, 2024).

Electric cars are most effective in regions with low-carbon electricity grids (International Transport Forum, 2020; Verma et al., 2022). This includes countries with high hydro power (including Iceland, Norway, Sweden, and parts of Canada such as British Columbia and Quebec), nuclear energy (such as France), and renewables (including Portugal, New Zealand, and parts of the United States, including California and some of the Northwest) (IEA, 2024). Electric car adoption is growing rapidly in a number of regions. For future scaling, targeting countries with supportive policies, renewable energy potential, and growing urban populations will deliver the greatest climate benefits.

Action Word
Mobilize
Solution Title
Electric Cars
Classification
Highly Recommended
Lawmakers and Policymakers
  • Create government procurement policies to transition government fleets to electric cars.
  • Provide financial incentives such as tax breaks, subsidies, or grants for electric car production and purchases that gradually reduce as market adoption increases.
  • Provide complimentary benefits for electric car drivers, such as privileged parking areas, free tolls, and access schemes.
  • Use targeted financial incentives to assist low-income communities in purchasing electric cars and to incentivize manufacturers to produce more affordable options.
  • Develop charging infrastructure, ensuring adequate spacing between stations and equitable distribution of stations.
  • Invest in R&D or implement regulations to improve manufacturing, adoption, supply chain standards, and circularity of electric cars, particularly batteries.
  • Transition fossil fuel electricity production to renewables while promoting the transition to electric cars.
  • Disincentivize fossil fuel–powered car ownership by gradually introducing taxes, penalties, buy-back programs, or other mechanisms.
  • Offer educational resources and one-stop shops for information on electric vehicles, including demonstrations, cost savings, environmental impact, and maintenance.
  • Work with industry and labor leaders to construct new electric car plants and to transition fossil fuel–powered car manufacturing into electric car production.
  • Set regulations for sustainable use of electric car batteries and improve recycling infrastructure.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Incentivize or mandate life-cycle assessments and product labeling (e.g., Environmental Product Declarations).
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Practitioners
  • Produce and sell affordable electric car models.
  • Collaborate with dealers to provide incentives, low-interest financing, or income-based payment options.
  • Develop charging infrastructure, ensuring adequate spacing between stations and equitable distribution of stations.
  • Invest in R&D to improve manufacturing, adoption, supply chain standards, and circularity of electric cars, particularly batteries.
  • Offer educational resources and one-stop shops for information on electric cars, including demonstrations, cost savings, environmental impact, and maintenance.
  • Work with policymakers and labor leaders to construct new electric car plants and to transition fossil fuel–powered car manufacturing into electric car production.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Invest in recycling and circular economy infrastructure.
  • Conduct life-cycle assessments and ensure product labeling (e.g., Environmental Product Declarations).
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Business Leaders
  • Set company procurement policies to transition corporate fleets to electric cars.
  • Take advantage of any financial incentives such as tax breaks, subsidies, or grants for electric car purchases.
  • Create long-term purchasing agreements with electric car manufacturers to support stable demand and improve economies of scale.
  • Install charging stations and offer employee benefits for electric car drivers, such as privileged parking areas.
  • Invest in R&D to improve manufacturing, adoption, supply chain standards, and circularity of electric cars, particularly batteries.
  • Work with industry and labor leaders to transition fossil fuel–powered car manufacturing into electric car production.
  • Advocate for financial incentives and policies that promote electric car adoption.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Educate customers and investors about the company's transition to electric cars and encourage them to learn more about them.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Nonprofit Leaders
  • Set organizational procurement policies to transition fleets to electric cars.
  • Take advantage of financial incentives such as tax breaks, subsidies, or grants for electric car purchases.
  • Advocate for financial incentives and policies that promote electric car adoption.
  • Install charging stations and offer employee benefits for electric car drivers, such as privileged parking areas.
  • Advocate for or provide improved charging infrastructure.
  • Offer workshops or support to low-income communities for purchasing and owning electric cars.
  • Work with industry and labor leaders to transition fossil fuel–powered car manufacturing into electric car production.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Advocate for regulations on lithium-ion batteries and investments in recycling facilities.
  • Offer educational resources and one-stop shops for information on electric cars, including demonstrations, cost savings, environmental impact, and maintenance.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Investors
  • Invest in electric car companies.
  • Support portfolio companies in transitioning their corporate fleets.
  • Invest in companies that provide charging equipment or installation.
  • Invest in R&D to improve manufacturing, adoption, supply chain standards, and circularity of electric cars, particularly batteries.
  • Invest in electric car companies, associated supply chains, and end-user businesses like rideshare apps.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption. 

Further information:

Philanthropists and International Aid Agencies
  • Set organizational procurement policies to transition fleets to electric cars.
  • Install charging stations and offer employee benefits for electric car drivers, such as privileged parking areas.
  • Take advantage of any financial incentives such as tax breaks, subsidies, or grants for electric car purchases.
  • Advocate for financial incentives and policies that promote electric car adoption.
  • Advocate for or provide improved charging infrastructure.
  • Offer financial services such as low-interest loans or grants for purchasing electric cars and charging equipment.
  • Offer workshops or support to low-income communities for purchasing and owning electric cars.
  • Work with industry and labor leaders to transition fossil fuel–powered car manufacturing into electric car production.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Advocate for regulations on lithium-ion batteries and investments in recycling facilities.
  • Offer educational resources and one-stop shops for information on electric cars, including demonstrations, cost savings, environmental impact, and maintenance.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Thought Leaders
  • If purchasing a new car, buy an electric car.
  • Take advantage of financial incentives such as tax breaks, subsidies, or grants for electric car purchases.
  • Share your experiences with electric cars through social media and peer-to-peer networks, highlighting the cost savings, benefits, incentive programs, and troubleshooting tips.
  • Advocate for financial incentives and policies that promote electric car adoption.
  • Advocate for improved charging infrastructure.
  • Help improve the circularity of electric car supply chains through design, advocacy, or implementation.
  • Conduct in-depth life-cycle assessments of electric cars in particular geographies.
  • Research ways to reduce weight and improve the performance of electric cars while appealing to customers.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Technologists and Researchers
  • Improve the circularity of supply chains for electric car components.
  • Reduce the amount of critical minerals required for electric car batteries.
  • Innovate low-cost methods to improve safety, labor standards, and supply chains in mining for critical minerals.
  • Research ways to reduce weight and improve the performance of electric cars while appealing to customers.
  • Develop vehicle-grid integration and feasible means of using the electrical capacity of electric cars to manage the broader grid.
  • Improve techniques to repurpose used electric car batteries for stationary energy storage.
  • Develop methods of converting fossil fuel–powered car manufacturing and infrastructure to electric.

Further information:

Communities, Households, and Individuals
  • If purchasing a new car, purchase an electric car.
  • Take advantage of any financial incentives such as tax breaks, subsidies, or grants for electric car purchases.
  • Share your experiences with electric cars through social media and peer-to-peer networks, highlighting the cost-savings, benefits, incentive programs, and troubleshooting tips.
  • Help shift the narrative around electric cars by demonstrating capability and performance.
  • Advocate for financial incentives and policies that promote electric car adoption.
  • Advocate for improved charging infrastructure.
  • Help improve ciricularity of electric car supply chains.
  • Join international efforts to promote and ensure that environmental and human rights standards are met for supply chains.
  • Create, support, or join partnerships that offer information, training, and general support for electric car adoption.

Further information:

Sources
Evidence Base

Consensus of effectiveness in reducing emissions: Mixed

There is a high level of consensus among major organizations and researchers working on climate solutions that electric cars offer a substantial reduction in GHG emissions compared to fossil fuel–powered cars. This advantage is strongest in places where electricity in the grid comes from sources with low GHG emissions, but it persists even if fossil fuels play a major role in energy production. 

Major climate research organizations generally see electric cars as the primary means of reducing GHG emissions from passenger transportation. This perspective has received criticism from some scholars who argue that electric cars have been overstated as a climate solution, pointing to supply constraints, embodied emissions, and emissions from electricity generation (Jones, 2019; Milovanoff et al., 2020). Embodied emissions are outside the scope of this assessment. 

The Intergovernmental Panel on Climate Change (IPCC) (2022) estimated well-to-wheel (upstream and downstream emissions) GHG emissions intensity from gasoline and diesel cars at 139 g CO₂‑eq/pkm and 107 g CO₂‑eq/pkm, respectively. They estimated that electric cars running on low-carbon electricity (solar, wind, and nuclear sourced) emit 9 g CO₂‑eq/pkm; electric cars running on natural gas electricity emit 104 g CO₂‑eq/pkm; and electric cars running entirely on coal electricity emit 187 g CO₂‑eq/pkm. These estimates include upstream emissions, such as those from oil refining and coal mining.

The International Energy Agency (IEA, 2024) noted that “[a] battery electric car sold in 2023 will emit half as much as fossil fuel–powered equivalents over its lifetime. This includes full life-cycle emissions, including those from producing the car.” 

The International Transport Forum (ITF) (2020) estimated that fossil fuel–powered cars emit 162 g CO₂‑eq/pkm, while electric cars emit 125 g CO₂‑eq/pkm. This included embodied and upstream emissions, which are outside the scope of this assessment.

The results presented in this document summarize findings from 15 reviews and meta-analyses and 24 original studies reflecting current evidence from 52 countries, primarily the IEA’s Electric Vehicle Outlook (2024), the Electric Vehicle Database (2024), the International Transportation Forum’s life cycle analysis on sustainable transportation (2020), and the Nickel Institute’s cost estimates on electric cars (Nickel Institute, 2021a, 2021b, 2021c). We recognize this limited geographic scope creates bias, and hope this work inspires research and data sharing on this topic in underrepresented regions.

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