Production of biochar (the carbon (C)-rich solid formed by pyrolysis of biomass) and its storage in soils have been suggested as a means of abating climate change by sequestering carbon, while simultaneously providing energy and increasing crop yields. Substantial uncertainties exist, however, regarding the impact, capacity and sustainability of biochar at the global level. In this paper we estimate the maximum sustainable technical potential of biochar to mitigate climate change. Annual net emissions of carbon dioxide (CO2), methane and nitrous oxide could be reduced by a maximum of 1.8 Pg CO2-C equivalent (CO2-Ce) per year (12% of current anthropogenic CO2-Ce emissions; 1 Pg=1 Gt), and total net emissions over the course of a century by 130 Pg CO2-Ce, without endangering food security, habitat or soil conservation. Biochar has a larger climate-change mitigation potential than combustion of the same sustainably procured biomass for bioenergy, except when fertile soils are amended while coal is the fuel being offset.
Since 2000, anthropogenic carbon dioxide (CO2) emissions have risen by more than 3% annually1, putting Earth's ecosystems on a trajectory towards rapid climate change that is both dangerous and irreversible2. To change this trajectory, a timely and ambitious programme of mitigation measures is needed. Several studies have shown that, to stabilize global mean surface temperature, cumulative anthropogenic greenhouse-gas (GHG) emissions must be kept below a maximum upper limit, thus indicating that future net anthropogenic emissions must approach zero2,3,4,5,6. If humanity oversteps this threshold of maximum safe cumulative emissions (a limit that may already have been exceeded7), no amount of emissions reduction will return the climate to within safe bounds. Mitigation strategies that draw down excess CO2 from the atmosphere would then assume an importance greater than an equivalent reduction in emissions.
Production of biochar, in combination with its storage in soils, has been suggested as one possible means of reducing the atmospheric CO2 concentration (refs 8,9,10,11,12,13 and see also Supplementary Note for a history of the concept and etymology of the term). Biochar's climate-mitigation potential stems primarily from its highly recalcitrant nature14,15,16, which slows the rate at which photosynthetically fixed carbon (C) is returned to the atmosphere. In addition, biochar yields several potential co-benefits. It is a source of renewable bioenergy; it can improve agricultural productivity, particularly in low-fertility and degraded soils where it can be especially useful to the world's poorest farmers; it reduces the losses of nutrients and agricultural chemicals in run-off; it can improve the water-holding capacity of soils; and it is producible from biomass waste17,18. Of the possible strategies to remove CO2 from the atmosphere, biochar is notable, if not unique, in this regard.
Biochar can be produced at scales ranging from large industrial facilities down to the individual farm19, and even at the domestic level20, making it applicable to a variety of socioeconomic situations. Various pyrolysis technologies are commercially available that yield different proportions of biochar and bioenergy products, such as bio-oil and syngas. The gaseous bioenergy products are typically used to generate electricity; the bio-oil may be used directly for low-grade heating applications and, potentially, as a diesel substitute after suitable treatment21. Pyrolysis processes are classified into two major types, fast and slow, which refer to the speed at which the biomass is altered. Fast pyrolysis, with biomass residence times of a few seconds at most, generates more bio-oil and less biochar than slow pyrolysis, for which biomass residence times can range from hours to days.
The sustainable-biochar concept is summarized in Figure 1. CO2 is removed from the atmosphere by photosynthesis. Sustainably procured crop residues, manures, biomass crops, timber and forestry residues, and green waste are pyrolysed by modern technology to yield bio-oil, syngas, process heat and biochar. As a result of pyrolysis, immediate decay of these biomass inputs is avoided. The outputs of the pyrolysis process serve to provide energy, avoid emissions of GHGs such as methane (CH4) and nitrous oxide (N2O), and amend agricultural soils and pastures. The bioenergy is used to offset fossil-fuel emissions, while returning about half of the C fixed by photosynthesis to the atmosphere. In addition to the GHG emissions avoided by preventing decay of biomass inputs, soil emissions of GHGs are also decreased by biochar amendment to soils. The biochar stores carbon in a recalcitrant form that can increase soil water- and nutrient-holding capacities, which typically result in increased plant growth. This enhanced productivity is a positive feedback that further enhances the amount of CO2 removed from the atmosphere. Slow decay of biochar in soils, together with tillage and transport activities, also returns a small amount of CO2 to the atmosphere. A schematic of the model used to calculate the magnitudes of these processes is shown as Supplementary Figure S1.
Even under the most zealous investment programme, biochar production will ultimately be limited by the rate at which biomass can be extracted and pyrolysed without causing harm to the biosphere or to human welfare. Globally, human activity is responsible for the appropriation of 16 Pg C per year from the biosphere, which corresponds to 24% of potential terrestrial net primary productivity (NPP)22. Higher rates of appropriation will increase pressure on global ecosystems, exacerbating a situation that is already unsustainable23.
The main aim of this study is to provide an estimate of the theoretical upper limit, under current conditions, to the climate-change mitigation potential of biochar when implemented in a sustainable manner. This limit, which we term the maximum sustainable technical potential (MSTP), represents what can be achieved when the portion of the global biomass resource that can be harvested sustainably (that is, without endangering food security, habitat or soil conservation) is converted to biochar by modern high-yield, low-emission, pyrolysis methods. The fraction of the MSTP that is actually realized will depend on a number of socioeconomic factors, including the extent of government incentives and the relative emphasis placed on energy production relative to climate-change mitigation. Aside from assuming a maximum rate of capital investment that is consistent with that estimated to be required for climate-change mitigation24, this study does not take into account any economic, social or cultural barriers that might further limit the adoption of biochar technology.
Our analysis shows that sustainable global implementation of biochar can potentially offset a maximum of 12% of current anthropogenic CO2-C equivalent (CO2-Ce) emissions (that is, 1.8 Pg CO2-Ce per year of the 15.4 Pg CO2-Ce emitted annually), and that over the course of a century, the total net offset from biochar would be 130 Pg CO2-Ce. We also show that conversion of all sustainably obtained biomass to maximize bioenergy, rather than biochar, production can offset a maximum of 10% of the current anthropogenic CO2-Ce emissions. The relative climate-mitigation potentials of biochar and bioenergy depend on the fertility of the soil amended and the C intensity of the fuel being offset, as well as the type of biomass. Locations at which the soil fertility is high and coal is the fuel being offset are best suited for bioenergy production. The climate-mitigation potential of biochar (with combined energy production) is higher for all other situations.
Sustainable biomass-feedstock availability
To ensure that our estimates represent a sustainable approach, we use a stringent set of criteria to assess potential feedstock availability for biochar production. Of primary importance is the conversion of land to generate feedstock. In addition to its negative effects on ecosystem conservation, land clearance to provide feedstock may also release carbon stored in soils and biomass, leading to unacceptably high carbon-payback times before any net reduction in atmospheric CO2 is achieved (ref. 25, Supplementary Methods and Supplementary Fig. S2). For example, we find that a land-use change carbon debt greater than 22 Mg C ha−1 (an amount that would be exceeded by conversion of temperate grassland to annual crops25) will result in a carbon-payback time that is greater than 10 years. Clearance of rainforests to provide land for biomass-crop production leads to carbon payback times in excess of 50 years. Where rainforest on peatland is converted to biomass-crop production, carbon-payback times may be in the order of 325 years. We therefore assume that no land clearance will be used to provide biomass feedstock, nor do we include conversion of agricultural land from food to biomass-crop production as a sustainable source of feedstock, both because of the negative consequences for food security and because it may indirectly induce land clearance elsewhere26. Some dedicated biomass-crop production on abandoned, degraded agricultural soil has been included in this study as this will not adversely affect food security27 and can improve biodiversity28,29. We further assume that extraction rates of agricultural and forestry residues are sufficiently low to preclude soil erosion or loss of soil function, and that no industrially treated waste biomass posing a risk of soil contamination will be used.
Other constraints on biochar production methods arise because emissions of CH4, N2O, soot or volatile organic compounds combined with low biochar yields (for example, from traditional charcoal kilns or smouldering slash piles) may negate some or all of the carbon-sequestration benefits, cause excessive carbon-payback times or be detrimental to health. Therefore, we do not consider any biochar production systems that rely on such technologies, and restrict our analysis to systems in which modern, high-yield, low-emission pyrolysis technology can feasibly be used to produce high-quality biochar.
Within these constraints, we derived a biomass-availability scenario for our estimate of MSTP, as well as two additional scenarios, Alpha and Beta, which represent lower demands on global biomass resources (Table 1). Attainment of the MSTP would require substantial alteration to global biomass management, but would not endanger food security, habitat or soil conservation. The Alpha scenario restricts biomass availability to residues and wastes available using current technology and practices, together with a moderate amount of agroforestry and biomass cropping. All three scenarios represent fairly ambitious projects, and require progressively greater levels of political intervention to promote greater adoption of sustainable land-use practices and increase the quantity of uncontaminated organic wastes available for pyrolysis. We do not consider any scenarios that are not ambitious in this study, as the intention is to investigate whether biochar could make a substantial contribution to climate-change mitigation—an aspiration that certainly will not be accomplished by half-hearted measures. The range of mitigation results reported thus refers only to the scenarios considered and does not encompass the full range of less-effective outcomes corresponding to varying levels of inaction. The scenarios are based on current biomass availability (Supplementary Methods and Supplementary Tables S1 and S2), the composition and energy contents of different types of biomass and the biochar derived from each (Supplementary Tables S3 and S4), and the rate of adoption of biochar technology (Supplementary Fig. S3). How this biomass resource base changes over the course of 100 years will depend on the potential effects of changing climate, atmospheric CO2, sea level, land use, agricultural practices, technology, population, diet and economic development. Some of these factors may increase biomass availability and some may decrease it. A full assessment of the wide range of possible future scenarios within plausible ranges of these factors remains outside the scope of this study.
Avoided GHG emissions
Results for the three scenarios are expressed below as a range from the Alpha scenario first to the MSTP last. The model predicts that maximum avoided emissions of 1.0–1.8 Pg CO2-Ce per year are approached by mid-century and that, after a century, the cumulative avoided emissions are 66–130 Pg CO2-Ce (Fig. 2). Half of the avoided emissions are due to the net carbon sequestered as biochar, 30% to replacement of fossil-fuel energy by pyrolysis energy and 20% to avoided emissions of CH4 and N2O. Cumulative and annual avoided emissions for the individual gases CO2, CH4 and N2O are given in Supplementary Figures S4, S5 and S6.
A detailed breakdown of the sources of cumulative avoided GHG emissions over 100 years is given in Figure 3. The two most important factors contributing to the avoided emissions from biochar are carbon stored as biochar in soil (43–94 Pg CO2-Ce) and fossil-fuel offsets from coproduction of energy (18–39 Pg CO2-Ce).
Of the beneficial feedbacks, the largest is due to avoided CH4 emissions from biomass decomposition (14–17 Pg CO2-Ce), predominantly arising from the diversion of rice straw from paddy fields (see Supplementary Table S5 for estimate of the mean CH4 emission factor). The next largest positive feedbacks, in order of decreasing magnitude, arise from biochar-enhanced NPP on cropland, which contributes 9–16 Pg CO2-Ce to the net avoided emissions (if these increased crop residues are converted to biochar), followed by reductions in soil N2O emissions (4.0–6.2 Pg CO2-Ce), avoided N2O emissions during biomass decomposition (1.8–3.3 Pg CO2-Ce) and enhanced CH4 oxidation by dry soils (0.44–0.8 Pg CO2-Ce).
Of the adverse feedbacks, biochar decomposition is the largest (8–17 Pg CO2-Ce), followed by loss of soil organic carbon due to diversion of biomass from soil into biochar production (6–10 Pg CO2-Ce), and transport (1.3–1.9 Pg CO2-Ce, see Supplementary Fig. S7). Contributions to the overall GHG budget from tillage (0.03–0.044 Pg CO2-Ce) and reduced N-fertilizer production (0.2–0.3 Pg CO2-Ce) are negligible (although their financial costs may not be).
The relative importance of all these factors to the GHG budget varies considerably among feedstocks. Notably, rice residues, green waste and manure achieve the highest ratios of avoided CO2-Ce emissions per unit of biomass-carbon (1.2–1.1, 0.9 and 0.8 CO2-Ce/C, respectively) because of the benefits of avoided CH4 emissions.
Sensitivity and Monte Carlo analyses
Sensitivity and Monte Carlo analyses with respect to reasonable values of key variables were used to estimate the uncertainty of the model results; they suggest areas in which future research is most needed and provide guidance on how biochar production systems might be optimized (Fig. 4).
The strongest sensitivity is to the half-life of the recalcitrant fraction of biochar (see also Supplementary Table S6). Net avoided GHG emissions vary by −22% to +4% from that obtained using the baseline assumption of 300 years. However, most of this variation occurs for half-life <100 years, in which range we find (in agreement with previous work30) that sensitivity to this factor is high. Conversely, for a more realistic half-life of the recalcitrant fraction (>100 years), sensitivity to this factor is low because biochar can be produced much more rapidly than it decays. As currently available data suggest that the half-life of biochar's recalcitrant fraction in soil is in the millennial range (see Supplementary Methods, Supplementary Table S6 and refs 8,15,16,318, 15, 16, 31), the contribution of its decay to the net GHG balance over centennial timescales is likely to be small.
The next largest sensitivity is to the pyrolysis carbon yield (−9% to +11%), indicating the importance of engineering to optimize for high yields of biochar rather than for energy production. This will be constrained, however, by the sensitivity to the labile fraction of the biochar (−7% to +4%), which indicates the importance of optimizing for production of recalcitrant biochar rather than for higher yields of lower-quality biochar.
After carbon yield, the next largest sensitivity is to the carbon intensity of the fuel offset by pyrolysis energy production, with net avoided emissions varying by −4% from the baseline assumption when natural gas is the fuel being offset and by +15% when coal is offset.
Varying the impact of biochar amendment on soil N2O emissions from zero to the largest reported reduction (80%; ref. 32) produces a sensitivity of −4% to +11%. Further variability in the impact of biochar on N2O emissions arises from adjusting the fraction of biomass-N that (if left to decompose) would be converted to N2O-N, from the Intergovernmental Panel on Climate Change default values assumed in this study up to the higher rate of 5% suggested by more recent work33,34. This would increase the net avoided GHG emissions by up to 8%.
Uncertainty in the response of crop yields to biochar amendment results in estimated range of −6% to +7% in the impact of enhanced NPP of cropland on net avoided GHG emissions.
Sensitivities to the pyrolysis energy efficiency (±5%), to the half-life of the biochar's labile fraction (−4% to +1%) and to its impact on soil CH4 oxidation (± 1%) are small.
The net effect of covariance of the above factors was assessed using the Monte Carlo analysis (n=1,000, Supplementary Table S7). Despite limited data on the decomposition rate of biochar in soils and the effects of biochar additions on soil GHG fluxes, sensitivity within realistic ranges of these parameters is small, resulting in an estimated uncertainty of ±8 to 10% (±1 s.d.) in the cumulative avoided GHG emissions for the three scenarios.
Comparison of biochar and bioenergy approaches
The mitigation impact of the renewable energy obtained from both biochar production and biomass combustion depends on the carbon intensity (that is, the mass of carbon emitted per unit of total energy produced) of the offset energy sources11. At our baseline carbon intensity (17.5 kg C GJ−1; see Methods section), the model predicts that, on an average, the mitigation impact of biochar is 27–22% (14–23 Pg CO2-Ce) larger than the 52–107 Pg CO2-Ce predicted if the same sustainably procured biomass were combusted to extract the maximum amount of energy (Fig. 2). This advantage of biochar over bioenergy is largely attributable to the beneficial feedbacks from enhanced crop yields and soil GHG fluxes (Fig. 3, Supplementary Fig. S8).
Because the principal contribution of biomass combustion to avoided GHG emissions is the replacement of fossil fuels (Fig. 3), the bioenergy approach shows a considerably higher sensitivity to carbon intensity than does biochar (Fig. 5). The carbon intensity of offset energy varies from near-zero for renewable and nuclear energy to 26 kg C GJ−1 for coal combustion35. Mean cumulative avoided emissions from biochar and biomass combustion are equal in our scenarios when the carbon intensity of offset energy is 26–24 kg C GJ−1 (Fig. 5). In the MSTP scenario, this corresponds to an energy mix to which coal combustion contributes about 80%, whereas in the Alpha scenario, the mean mitigation benefit of biochar remains higher than that of bioenergy, even when 100% coal is offset. The cumulative avoided emissions from both strategies decrease as the carbon intensity of the offset energy mix decreases, but the rate of decrease for biomass combustion is 2.5–2.7 times greater than that for biochar. As expected, the cumulative avoided emissions for biomass combustion are essentially zero when the carbon intensity of the energy mix is also zero. In contrast, the cumulative avoided emissions for biochar are still substantial at 48–91 Pg CO2-Ce.
Given that much of the increased climate mitigation from biochar relative to biomass combustion stems from the beneficial feedbacks of adding biochar to soil, and that these feedbacks will be greatest on the least fertile soils, the relative mitigation potentials will vary regionally with soil type (see Supplementary Methods, Supplementary Fig. S9 and Supplementary Tables S8–S11 for an account of how these feedbacks are calculated). The distribution of soils of varying fertility on global cropland is shown in Figure 6. Globally, 0.31 Gha of soils with no fertility constraints are in use as cropland, as well as 0.29 Gha of cropland with few fertility constraints, 0.21 Gha with slight constraints, 0.32 Gha with moderate constraints, 0.18 Gha with severe constraints, 0.13 Gha with very severe constraints and 0.09 Gha of cropland on soils categorized as unsuitable for crop production. The amount of biomass produced in soils of different fertilities is shown in Supplementary Table S12. Figure 7 shows how the climate mitigation from biochar varies relative to biomass combustion when both soil fertility and the carbon intensity of energy offsets are considered. The relative benefit of producing biochar compared with biomass combustion is greatest when biochar is added to marginal lands and the energy produced by pyrolysis is used to offset natural gas, renewable or nuclear energy. When biochar is added to the most infertile cropland to offset the current global primary energy mix (Mw), which has a carbon intensity of 16.5 kg C GJ−1, the relative benefit from biochar is as much as 79–64% greater than that from bioenergy (Fig. 7, Supplementary Fig. S10). This net benefit diminishes as more coal is offset and as biochar is added to soils with higher fertility. Nevertheless, with the exception of those geographical regions having both naturally high soil fertility and good prospects for offsetting coal emissions (in which bioenergy yields up to 16–22% greater mitigation impact than biochar), biochar shows a greater climate-mitigation potential than bioenergy. The relative benefit of producing biochar compared with bioenergy is greatest when biomass crops are used as feedstocks (Fig. 7b), because avoided CH4 emissions from the use of manure, green waste and rice residues occur regardless of whether these other feedstocks are used for energy or biochar.
Our analysis demonstrates that sustainable biochar production (with addition to soils) has the technical potential to make a substantial contribution to mitigating climate change. Maximum avoided emissions of the order of 1.8 Pg CO2-Ce annually, and of 130 Pg CO2-Ce over the course of a century, are possible at current levels of feedstock availability, while preserving biodiversity, ecosystem stability and food security.
The biochar scenarios described here, with their very high levels of biomass utilization, are not compatible with simultaneous implementation of an ambitious biomass energy strategy. The opportunity cost of this forgone energy resource must be taken into account in an economic comparison of the two strategies. However, in terms of their potentials for climate-change mitigation, the mitigation impact of biochar is about one-fourth larger, on an average, than that obtained if the same biomass were combusted for energy. Regional deviations from this average are large because of differences in soil fertility and available biomass. Our model predicts that the relative climate-mitigation benefit of biochar compared with bioenergy is greatest in regions in which poor soils growing biomass crops can benefit most from biochar additions. In contrast, biomass combustion leads to a greater climate-mitigation impact in regions with fertile soils where coal combustion can be effectively offset by biomass energy production. The global climate-mitigation potential achievable from the use of terrestrial biomass may thus be maximized by a mixed strategy favouring bioenergy in those regions with fertile soils where coal emissions can be offset, and biochar elsewhere. Nevertheless, we have included biochar production in fertile, coal-intensive regions in our scenarios because other potential benefits of biochar, such as its potential for more efficient use of water and crop nutrients36,37,38, may favour its use even in such regions.
We emphasize that the results presented here assume that future biochar production follows strict sustainability criteria. Land-use changes that incur high carbon debts and biochar production using technologies with poorly controlled emissions lead to both large reductions in avoided emissions and excessively long carbon-payback times, during which net emissions are increased before any net reduction is observed. Biochar production and use, therefore, must be guided by well-founded and well-enforced sustainability protocols if its potential for mitigating climate change is to be realized.
A model (BGRAM version 1.1) to calculate the net avoided GHG emissions attributable to sustainable biochar production as a function of time was developed and applied to the three scenarios. This model includes the effects of feedstock procurement, transport, pyrolysis, energy production, soil incorporation, soil GHG flux, soil fertility and fertilizer use (see also Supplementary Table S13), and biomass and biochar decomposition (see also Supplementary Fig. S11). The net avoided GHG emissions due to biochar were calculated as the difference between the CO2-equivalent emissions from biochar production and those that would have occurred as the biomass decomposed by other means had it not been converted to biochar. All emissions (actual or avoided) were calculated with time dependency. Wherever possible, conservative assumptions were used to provide a high degree of confidence that our results represent a conservative estimate of the avoided GHG emissions achievable in each scenario. A detailed account of both the model and the three scenarios is given in Supplementary Methods.
Biochar can be produced sustainably or unsustainably. Our criteria for sustainable biochar production require that biomass procured from agricultural and silvicultural residues be extracted at a rate and in a manner that does not cause soil erosion or soil degradation; crop residues currently in use as animal fodder not be used as biochar feedstock; minimal carbon debt be incurred from land-use change or use of feedstocks with a long life expectancy; no new lands be converted into biomass production and no agricultural land be taken out of food production; no biomass wastes that have a high probability of contamination, which would be detrimental to agricultural soils, be used; and biomass crop production be limited to production on abandoned agricultural land that has not subsequently been converted to pasture, forest or other uses. We further require that biochar be manufactured using modern technology that eliminates soot, CH4 and N2O emissions while recovering some of the energy released during the pyrolysis process for subsequent use.
We consider three GHGs in this analysis: CO2, CH4 and N2O (see Supplementary Table S14 for a summary of estimated global warming potentials for these GHGs). Although the different atmospheric lifetimes of these gases ensure that there is no equivalence among them in any strict sense, we nevertheless adopt the common practice of normalizing each gas to a 'CO2-C equivalent' using the estimated radiative forcing produced by the emission of each gas, integrated over a 100-year period following emission, using Intergovernmental Panel on Climate Change 100-year global warming potentials39 of 23 for CH4and 296 for N2O.
Comparison with bioenergy
To compare the net avoided GHG emissions stemming from biochar with those from bioenergy production, we apply the same model and sustainability criteria, but assume complete combustion to liberate the maximum possible energy, rather than slow pyrolysis, as the conversion technology.
Soil application and fertility classification
Maximum biochar application to the top 0.15 m of agricultural soils was assumed to be 50 Mg C ha−1. It was assumed that only 20% of pasture soils will receive these application rates because of constraints from terrain, accessibility, fire and wind. See Supplementary Methods and Supplementary Figure S12.
Soil-fertility classifications were taken from ref. 40. These were combined with a 5-minute resolution map of global cropland distribution41 to produce a global map of cropland, categorized by the severity of soil-fertility constraints (Fig. 6).
Carbon intensity of fuel offsets
The baseline carbon intensity of the fuel offsets (Mb) used here is 17.5 kg C GJ−1. The current world primary-energy mix (Mw) has a carbon intensity of 16.5 kg C GJ−1 and the current world electricity-generation mix (Mew) has a carbon intensity of 15 kg C GJ−1 (ref. 42). See Supplementary Methods for the derivation of these carbon intensities.
Technology adoption rate
The rate at which installed biochar production capacity approaches its maximum is constrained by simple economic considerations. Data for estimated capital costs are shown in Supplementary Table S15. These are implemented in the model using a Gompertz curve (Supplementary Methods). The model allows for a lead time of 5 years, during which little plant capacity is commissioned. Slow-to-moderate investment for the remainder of the first decade and rapid adoption over the following three decades at a rate of capital investment consistent with the 2% of global gross domestic product that Lord Stern estimates to be required for climate-change mitigation24 culminate in near-maximal biochar production rates after a total of four decades. Net avoided GHG emissions over the first decade are negligible, because of a combination of initially slow adoption and carbon-debt payback.
How to cite this article: Woolf, D. et al. Sustainable biochar to mitigate global climate change. Nat. Commun. 1:56 doi: 10.1038/ncomms1053 (2010).
Raupach, M. R. et al. Global and regional drivers of accelerating CO2 emissions. PNAS 104, 10288–10293 (2007).
Solomon, S., Plattner, G., Knutti, R. & Friedlingstein, P. Irreversible climate change due to carbon dioxide emissions. PNAS 106, 1704–1709 (2009).
Broecker, W. S. Climate change: CO2 arithmetic. Science 315, 1371 (2007).
Matthews, H. D. & Caldeira, K. Stabilizing climate requires near-zero emissions. Geophys. Res. Lett. 35, L04705 (2008).
Allen, M. R. et al. Warming caused by cumulative carbon emissions towards the trillionth tonne. Nature 458, 1163–1166 (2009).
Meinshausen, M. et al. Greenhouse-gas emission targets for limiting global warming to 2°C. Nature 458, 1158–1162 (2009).
Hansen, J. et al. Target atmospheric CO2: where should humanity aim? Open Atmos. Sci. J. 2, 217–231 (2008).
Sombroek, W. G., Nachtergaele, F.O. & Hebel, A. Amounts, dynamics and sequestering of carbon in tropical and subtropical soils. Ambio 22, 417–426 (1993).
Lehmann, J., Gaunt, J. & Rondon, M. Bio-char sequestration in terrestrial ecosystems—a review. Mitig. Adapt. Strat. Glob. Change 11, 403–427 (2006).
Glaser, B., Haumaier, L., Guggenberger, G. & Zech, W. The 'Terra Preta' phenomenon: a model for sustainable agriculture in the humid tropics. Naturwissenschaften 88, 37–41 (2001).
Fowles, M. Black carbon sequestration as an alternative to bioenergy. Biomass Bioenerg. 31, 426–432 (2007).
Laird, D. A. The charcoal vision: a win win win scenario for simultaneously producing bioenergy, permanently sequestering carbon, while improving soil and water quality. Agron. J. 100, 178–181 (2008).
Lehmann, J. A handful of carbon. Nature 447, 143–144 (2007).
Schmidt, M. W.I. & Noack, A.G. Black carbon in soils and sediments: analysis, distribution, implications, and current challenges. Global Biogeochem. Cy. 14, 777–793 (2000).
Kuzyakov, Y., Subbotina, I., Chen, H., Bogomolova, I. & Xu, X. Black carbon decomposition and incorporation into soil microbial biomass estimated by 14C labeling. Soil Biol. Biochem. 41, 210–219 (2009).
Cheng, C., Lehmann, J., Thies, J. E. & Burton, S. D. Stability of black carbon in soils across a climatic gradient. J. Geophys. Res. 113, doi:10.1029/2007JG000642 (2008).
Lehmann, D. J. & Joseph, S. Biochar for Environmental Management: Science and Technology (Earthscan Books Ltd, 2009).
Lenton, T. M. & Vaughan, N. E. The radiative forcing potential of different climate geoengineering options. Atmos. Chem. Phys. Discuss. 9, 2559–2608 (2009).
Lehmann, J. & Joseph, S. Chapter 9: biochar systems. in Biochar for Environmental Management: Science and Technology (eds Lehmann, J., Joseph, S.) (Earthscan Books Ltd, 2009).
Whitman, T. & Lehmann, J. Biochar—one way forward for soil carbon in offset mechanisms in Africa? Environ. Sci. Policy 12, 1024–1027 (2009).
Elliott, D. C. Historical developments in hydroprocessing bio-oils. Energy Fuels 21, 1792–1815 (2007).
Haberl, H. et al. Quantifying and mapping the human appropriation of net primary production in earth's terrestrial ecosystems. PNAS 104, 12942.
Wackernagel, M. et al. Tracking the ecological overshoot of the human economy. PNAS 99, 9266 (2002).
Stern, N. Testimony of Lord Nicholas Stern to the Committee on Energy and Commerce. At <http://archives.energycommerce.house.gov/cmte_mtgs/110-eaq-hrg.062608.Stern-Testimony.pdf> (2008).
Fargione, J., Hill, J., Tilman, D., Polasky, S. & Hawthorne, P. Land clearing and the biofuel carbon debt. Science 319, 1235–1238 (2008).
Searchinger, T. et al. Use of US croplands for biofuels increases greenhouse gases through emissions from land use change. Science 319, 1238–1240 (2008).
Field, C. B., Campbell, J. E. & Lobell, D. B. Biomass energy: the scale of the potential resource. Trends Ecol. Evol. 23, 65–72 (2008).
Tilman, D. et al. Beneficial biofuels—the food, energy, and environment trilemma. Science 325, 270–271 (2009).
Tilman, D., Hill, J. & Lehman, C. Carbon-negative biofuels from low-input high-diversity grassland biomass. Science 314, 1598–1600 (2006).
Gaunt, J. L. & Lehmann, J. Energy balance and emissions associated with biochar sequestration and pyrolysis bioenergy production. Environ. Sci. Technol. 42, 4152–4158 (2008).
Lehmann, J. et al. Australian climate-carbon cycle feedback reduced by soil black carbon. Nature Geosci. 1, 832–835 (2008).
Rondon, M., Ramirez, J. & Lehmann, J. Charcoal additions reduce net emissions of greenhouse gases to the atmosphere. Proc. 3rd USDA Sympos. on Greenhouse Gases and Carbon Sequestration 208 (2005).
Crutzen, P. J., Mosier, A. R., Smith, K. A. & Winiwarter, W. N2O release from agro-biofuel production negates global warming reduction by replacing fossil fuels. Atmos. Chem. Phys. Discuss 7, 11191–11205 (2007).
Del Grosso, S. J., Wirth, T., Ogle, S. M. & Parton, W. J. Estimating agricultural nitrous oxide emissions. Eos 89, 529–530 (2008).
Garg, A., Kazunari, K. & Pulles, P. 2006 IPCC Guidelines for National Greenhouse Gas Inventories, Volume 2: Energy (eds Eggleston, H.S., Buendia, L., Miwa, K., Ngara, T., Tanabe, K.) (IGES, 2006).
Tryon, E. Effect of charcoal on certain physical, chemical, and biological properties of forest soils. Ecol. Monogr. 81–115 (1948).
Steiner, C. et al. Nitrogen retention and plant uptake on a highly weathered central Amazonian Ferralsol amended with compost and charcoal. J. Plant Nutr. Soil Sc. 171, 893–899 (2008).
Lehmann, J. et al. Nutrient availability and leaching in an archaeological Anthrosol and a Ferralsol of the Central Amazon basin: fertilizer, manure and charcoal amendments. Plant Soil 249, 343–357 (2003).
Ramaswamy, V. et al. Chapter 6: radiative forcing of climate change. in Climate Change 2001: The Scientific Basis (eds Houghton, et al.) (CUP, 2001).
Fischer, G., van Velthuizen, H., Nachtergaele, F. & Medow, S. Global Agro-Ecological Assessment for Agriculture in the 21st Century (International Institute for Applied Systems Analysis & Food and Agriculture Organization of the United Nations, Laxenburg, Austria, 2002).
Erb, K. A comprehensive global 5 min resolution land-use data set for the year 2000 consistent with national census data. J. Land Use Sci. 2, 191–224 (2007).
International Energy Agency. Key World Energy Statistics: 2009 (IEA, 2009).
D.W. and F.A.S.-P. acknowledge support from the United Kingdom's Natural Environment Research Council (NERC) and Economic and Social Research Council (ESRC). J.E.A. acknowledges support from the United States' Department of Energy (USDOE) Office of Science, Office of Biological and Environmental Research, Climate and Environmental Science Division, Mitigation Science Focus Area and from the USDOE Office of Fossil Energy, Terrestrial Carbon Sequestration Program. The Pacific Northwest National Laboratory is operated for the USDOE by Battelle Memorial Institute under contract DE-AC05-76RL01830. J.L. acknowledges support from the Cooperative State Research Service of the U.S. Department of Agriculture and from the New York State Energy Research and Development Authority. S.J. acknowledges support from VenEarth Group LLC.
D.W., J.E.A., F.A.S.-P. and J.L. declare no competing financial interests. S.J. is Chairman of Anthroterra, a company conducting research into the development of a biochar mineral complex to replace conventional fertilizers. This company plans to manufacture and sell portable pyrolysers.
Supplementary Note, Supplementary Methods, Supplementary Figures, Supplementary Tables and Supplementary References
Supplementary Note, Supplementary Methods, Supplementary Figures S1–S12, Supplementary Tables S1–S15 and Supplementary References (PDF 899 kb)
Dataset represented in figure 3, comprising a breakdown of 100 years cumulative net avoided greenhouse gas emissions by feedstock and cause. (XLS 181 kb)
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Woolf, D., Amonette, J., Street-Perrott, F. et al. Sustainable biochar to mitigate global climate change . Nat Commun 1, 56 (2010). https://doi.org/10.1038/ncomms1053
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