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What might it cost to increase soil organic carbon using no-till on U.S. cropland?



Existing research provides estimates of the biophysical potential for increasing soil organic carbon (SOC) stock, however additional research is needed to enhance our understanding of the economic potential for agricultural soils to offset or help reduce CO2 emissions. This study derives the marginal cost to increase SOC sequestration by combining SOC sequestration potential estimates developed using the Intergovernmental Panel on Climate Change (IPCC) factors with an existing payment scheme that was designed to increase no-till (NT) adoption on U.S. cropland. The marginal costs of increasing SOC is a function of the amount of SOC that could be increased through NT and the expected cost to landowners of changing management to use NT.


The variability in SOC sequestration rates due to different land-use, management histories, climate, and soils, combined with the 48 unique payment rates to adopt NT, yield over 5,000 unique marginal cost values for increasing SOC sequestration. Nearly 95 percent of the biophysical potential SOC sequestration increase on U.S. cropland (2802 Tg CO2 from 140.1 Tg CO2 year−1 for 20 years) could be captured for less than $100 Mg−1 CO2. An estimated 64 to 93 percent of the biophysical potential could be captured for less than the low and high estimated costs to capture CO2 for geologic storage of $36.36 to $86.06 Mg−1 CO2, respectively.


Decreasing tillage intensity through adoption of no-till agriculture offers a cost-effective way to offset a portion of increasing global CO2 emissions. This research demonstrates that increasing SOC stocks through NT adoption can offset CO2 emissions at a lower cost than some other options for preventing CO2 from entering the atmosphere.


Global carbon dioxide (CO2) emissions are increasing every year [12]. While U.S. CO2 emissions declined between 2013 and 2017 from 5523 to 5271 Tg CO2 year−1 [13], measurements at Mauna Loa indicate that the atmospheric concentration of CO2 increased from around 400 to 410 ppm (parts per million) between 2015 and 2019 (NOAA [34]). A suite of strategies is likely required to prevent additional CO2 from entering the atmosphere through carbon capture and sequestration (CCS) and to remove CO2 from the atmosphere by increased afforestation, soil carbon sequestration, or directly removing CO2 from the atmosphere. Increasing soil organic carbon (SOC) stocks helps to reduce or offset CO2 emissions and helps to decrease the CO2 emissions that increase the atmospheric concentration levels of CO2. The ability for terrestrial systems to store or increase SOC varies spatially depending upon soil characteristics, climate, land-use, land-use change, and management. The SOC stock on cropland may be increased through decreased soil disturbance from tillage, removal of highly erodible land from crop production, reduced bare summer fallow, and inclusion of winter cover crops in the crop rotation [5, 8, 25, 26, 37, 38]. The biophysical potential SOC increase on U.S. agricultural land has been estimated using the method and factors developed by the Intergovernmental Panel on Climate Change (IPCC [45, 46]). Potential SOC sequestration increase on U.S. cropland of 233.6 Tg CO2 Eq year−1 (million metric tons of CO2 equivalent emissions; [44] could offset all US-Environmental Protection Agency (EPA) estimated average annual emission increases of 30.2 Tg CO2 Eq from all sources from 1990 to 2010 or nearly 43 percent of annual CO2 emissions from U.S. agriculture [13] for at least 20 years.

The economic potential to increase SOC stocks depends upon the cost to change management to increase SOC, the change in SOC that can be achieved, the cost of other CO2 emission mitigation activities, and the value of less CO2 entering the atmosphere. For SOC sequestration on U.S. agricultural land, the economic potential has been estimated using crop enterprise budgets and 2006 IPCC coefficients [43], mathematical programming and SOC sequestration rates using EPIC [30] or IPCC [29, 47], and econometric analysis and average SOC sequestration rates for the central U.S. [3]. Economic analyses of SOC sequestration have also been performed using similar approaches in Mali [11] and Senegal [10], Australia [28], and India [18]. These analyses compared the difference in profit between conventional tillage and no tillage implemented to increase SOC sequestration to determine the cost of the SOC sequestration. A common approach among these analyses was to vary the carbon price ($5 to $200 Mg−1 C) to evaluate the economic potential for SOC sequestration.

Increased no-till (NT) accounted for more than 50 percent of the potential increase in SOC sequestration in U.S. agricultural soils [44]. NT also helps to control soil erosion and runoff, increases water infiltration, enhances soil organic matter concentration, enhances biodiversity, may lower fuel costs, and creates other environmental benefits [27]. Despite these benefits, NT adoption by U.S. agriculture has been slow, with short-term NT (less than five continuous years) used on only 24 percent of the 111 Mha (million hectares) included in a study area in the U.S. [50]. Implementing NT may require new or modified equipment, different management skills, new pest problems to address, different herbicide applications, and other factors that may increase perceived risk [24].

To understand the slow adoption rates of NT, Knowler and Bradshaw [24] analyzed nearly 170 characteristics such as financial, education, age, acres planted, rainfall, etc., identified in 31 studies from 23 published articles to determine the factors that influence adoption of conservation agriculture. They found that as the number of studies that analyzed the same characteristics about willingness to adopt conservation tillage increased, the greater the likelihood of mixed results, thus making the issue less rather than more clear. The primary policy implication of their research is that there are no factors that influence conservation tillage adoption that are universally statistically significant, however financial assistance to help offset initial investments and transition costs seems to be effective [24].

Given the expected benefits to soil health from NT management yet its slow adoption, U.S. programs often address ways to reduce tillage intensity [6, 60] and encourage increased NT use through programs that help offset some of the investment and transition costs of adopting NT [55]. The expected payment necessary to encourage tillage that reduces soil disturbance may be used to help develop the marginal cost curves for carbon sequestration attained with NT. Little published data exist that provide the payment amount required to encourage landowners to adopt NT.

Based on crop enterprise budget data from twenty-three states that present a direct comparison, Sperow [43] found only four southern states where profit was higher using conventional tillage (CT) than NT for corn and soybean operations. Since research seems to indicate a profit advantage of NT over CT, yet adoption of long term NT is still limited, landowners may perceive that NT profit is lower and risk higher. In place of enterprise budgets, an alternative approach is to estimate the cost to convert from CT to NT using data from programs that were designed to enhance soil conservation. The USDA-NRCS administers the Environmental Quality Incentives Program (EQIP), a voluntary program that provides technical and financial assistance to agricultural producers for up to ten years for implementing conservation practices [55]. Practice Code/Name “329–Residue and Tillage Management–No-Till/Strip Till/ Direct Seed” was developed to reduce soil erosion, improve soil organic matter content, reduce carbon dioxide losses, reduce energy use, improve plant-available moisture, and enhance wildlife habitat by managing biomass residue on the soil surface year-round [57]. Each U.S. state provides the criteria for ranking applications to the program, eligible practices, payment rates, and other program requirements to participate in the program based on input from agribusiness, producer groups, conservation organizations, and representatives from other state and federal agencies [55].

The objective of this research is to estimate the cost of increasing SOC on cropland when tillage is reduced to NT. The cost of SOC stock changes from increased NT adoption was estimated using EQIP payments. The change to SOC stocks from conversion to NT was estimated using IPCC factors and data for soil carbon under native vegetation. The approach generates different carbon values (prices) across cropland for SOC sequestration rates that vary by climate, soil, management history, and land use history and the EQIP payment that varies by state. Biardeau et al. [4] used a similar approach using COMET-Planner to estimate SOC and EQIP payments to reflect the cost increase SOC stocks through crop rotation and the addition of mulch to management systems. The research presented here provides additional evidence that policies that encourage NT adoption are cost effective.

Results and discussion

The spatial distribution of NT agriculture across the U.S. at the beginning of the analysis in 1997 is from CTIC data (Fig. 1). Based upon the IPCC factors to account for climate, soil characteristics, soil disturbance through tillage, biomass input, and NRI crop data, total SOC stocks increased by NT adoption on U.S. cropland in 2017 was estimated to be 38.2 Tg C year−1 (140.1 Tg CO2 year−1), a rate that could be maintained for 20 years based on the IPCC assumed time to carbon stock equilibrium (Table 1; IPCC [21]). The weighted average SOC sequestration rate by tillage sequence ranged from 0.21 to 0.39 Mg C ha−1 year−1 (0.8 to 1.4 Mg CO2 year−1) with no SOC sequestration increase from cropland that was in NT for the final two periods (Table 1). The highest SOC sequestration rate resulted when the management was non-crop in the initial period before transitioning from CT to NT. The smallest SOC sequestration rate resulted from final transitions from reduced tillage (RT) to NT when cropland was CT or non-crop in the initial period.

Fig. 1
figure 1

Area of NT (ha) in 1997 based on long term adoption of NT from the Conservation Technology Information Center (CTIC)

Table 1 Area of U.S. cropland, soil disturbance sequence, total soil organic carbon stored (SOC) annually, total SOC stored after 20 years, and average rate of SOC storage

The tillage sequence CTCTNT provided the highest annual rate of SOC sequestration (27.6 Tg C year−1 (101.3 Tg CO2 year−1) or 72 percent of SOC stock increases of 2803 Tg CO2 over 20 years) on the largest area of cropland (72.3 Mha or 58 percent of all cropland) with an overall weighted average of 0.38 Mg C ha−1 year−1 (1.4 Mg CO2 year−1; Table 1). The next largest area (29 Mha or 26 percent of cropland) with the tillage sequence of CTRTNT contributed just over 16 percent of the total SOC sequestration potential (453 Tg CO2 (22.7 Tg CO2 year−1 for 20 years)) with an overall weighted average annual rate of 0.21 Mg C ha−1 year−1 (0.8 Mg CO2 year−1; Table 1). Combined, these activities accounted for over 88 percent of the increase in SOC stocks from NT adoption on 82.1 percent of the cropland. Agricultural land that was not under a crop (e.g., hay or pasture) in the first inventory, but was under NT in the final inventory following either CT or RT provided an additional 10.9 percent of the SOC sequestration potential on all cropland. Cropland areas with the highest annual SOC sequestration rates when NT was used during the final period with different tillage intensities for the first two periods are presented in Fig. 2. Cropland that transitioned from a lower to higher tillage intensity before NT adoption (e.g., RTCTNT) are not included in Table 1 because SOC increased by only 0.1 Tg CO2 year−1, with a majority of this increase only at a cost greater than $100 Mg−1 CO2.

Fig. 2
figure 2

Soil carbon sequestration rates (Mg C year−1 or Mg CO2 year−1) by tillage intensity sequence of CTCTNT (a) CTRTNT (b), and NCCTNT (c)

Total SOC sequestration rates provide a broad indication of the biophysical potential for carbon sequestration on cropland. Economic analysis requires information on a smaller scale to help determine the potential costs to increase SOC sequestration, which can help provide an estimate of the potential cost to offset CO2 emissions. To provide a better idea of the variability in SOC sequestration rates from NT, the weighted average annual SOC sequestration rates by tillage sequence and Farm Resource Region (USDA-ERS designations that depict geographic specialization in U.S. crop production [52]) are provided in Table 2. SOC sequestration rates ranged from 0.12 Mg C ha−1 year−1 (0.4 Mg CO2 ha−1 year−1) from the tillage sequence RTRTNT in the Southern Seaboard to 0.47 Mg C ha−1 year−1 (1.7 Mg CO2 ha−1 year−1) from tillage sequences CTCTNT and NCCTNT in the Northern Crescent Resource Region.

Table 2 Weighted average annual soil organic carbon sequestration rates to 30 cm depth by USDA-ERS Farm Resource Region and soil disturbance sequence

While only 48 unique EQIP annual payment rates were used to begin the analysis, when all possible tillage rotation sequences were considered, 5,058 unique carbon prices (cost to increase SOC stocks) that range from a low of $6.36 Mg−1 CO2 ($23.33 Mg−1 C) to $589.33 Mg−1 CO2 ($2,161 Mg−1 C) were generated. The lowest marginal cost occurred when the tillage sequence was CTCTNT in the cold temperate, moist region with a continuous row crop rotation on a high activity mineral soil with an estimated annual SOC sequestration rate of 2.86 Mg CO2 ha−1 year−1. The highest marginal cost occurred on a wheat fallow system in the warm temperate, dry climate region on a sandy soil when the tillage sequence was CTRTNT and the annual rate of SOC sequestration was estimated to be 0.22 Mg CO2 ha−1 year−1 (0.06 Mg C ha−1 year−1).

Just over 95 percent or 2660 Tg CO2 (133 Tg CO2 year−1 for 20 years), of the SOC that could be stored through NT adoption could be achieved for less than $100 Mg−1 CO2 and the marginal costs of achieving 2760 Tg CO2 (108.5 Tg CO2 year−1) or 77 percent of the potential SOC sequestration are less than $50 Mg−1 CO2. Above 108 Tg CO2 year−1 the marginal cost of SOC sequestration increased at an increasing rate. The marginal cost curves for increasing SOC stocks in agricultural soils from each tillage sequence are presented in Fig. 3. The least cost regions are predominantly in the midwestern counties, upper Great Plains, and upper northwest for both CTCTNT and CTRTNT tillage sequences (Fig. 4). The results indicate that the most expensive regions for increasing SOC sequestration are predominantly in the southern and southwestern states (Fig. 4) where NT adoption may not be as effective.

Fig. 3
figure 3

Marginal cost curves to increase soil carbon storage through NT based on EQIP payments for NT adoption based upon the sequence of tillage practices considered. The tillage sequence RTCTNT is not included because the contribution to SOC storage is negligible

Fig. 4
figure 4

Marginal cost of CO2 sequestration by U.S. county for CTCTNT (a) and CTRTNT (b) tillage

Crops respond differently to the amount of soil disturbance during crop production, so the effectiveness of NT depends on many factors [41, 61]. Toliver et al. [49] analyzed 30 years of refereed journal articles documenting 442 comparisons of CT to NT at 92 locations across the U.S. They determined that NT was not as effective on sandy soils where wheat and soybean yields were lower than with CT and that cotton and soybean yields increased with longer time under NT [49]. Rainfall was found to negatively affect crop yields when NT was applied, so NT may increase risk in regions with more annual rainfall. Toliver et al. [49] concluded that the crop, soil characteristics, and climate influence returns, risk, and adoption of NT. The change in average annual precipitation across the U.S., demonstrated with Fig. 5, which shows a gradient that, in general, goes from higher to lower annual moisture from east to west (PRISM Climate Group [39]). The exceptions are the Mississippi Delta region of the south and the far western edge of the Pacific Northwest with the highest annual average precipitation in the country. A comparison of Figs. 1, 2, 3, 4, 5 indicates that, for the most part, NT agriculture is not practiced in regions with high average annual rainfall, consistent with research findings.

Fig. 5
figure 5

Annual operation costs to convert from a conventional tillage to a no-till system estimated for 2014 ($ ha−1) and average rainfall by sate for 1981–2010

The expected costs of NT adoption should be higher in regions with higher precipitation where NT is not as effective. Figure 5 also provides the average cost-share payment for EQIP Practice 329 and precipitation distribution across the conterminous U.S. agricultural land. The highest EQIP payments are in NH, CT, TN, TX, MN, WY, and WA. Of these, only WA contains a high annual precipitation rate and WY was among the states with the lowest precipitation rates. The three lowest annual precipitation rates are all included within TX, which also has the second highest EQIP payment.

Marginal cost curves represent the cost to landowners of adopting NT relative to the amount of SOC that can be increased through the adoption of NT. These marginal cost curves (Fig. 3) demonstrate that there are some landowners that can increase SOC stocks for a lower cost than others. For this analysis, the cost curves represent the minimum CO2 price ($ Mg−1 CO2) required to encourage NT adoption to increase SOC sequestration. This carbon value provides a signal about the cost of one opportunity for addressing CO2 emission reductions. Nielsen et al. [33]. estimated that afforestation of cropland could sequester 60 to 130 Tg CO2 year−1 for $50 to $100 Mg−1 respectively, while Biardeau et al. [4] estimated costs of $32 to $442 Mg−1 CO2 from crop rotation changes and mulch respectively, which is similar to the results presented here. McKinsey and Company [31] provide negative costs for CO2 sequestration through tillage reduction globally, indicating that the incentive to adopt NT should be lower than estimated by EQIP and that the profit from crop production under NT is likely larger than CT profit.

Globally, CCS projects that are either under construction or currently operating capture and store about 40 Tg CO2 per year [16]. A comparison of the cost to store CO2 in geologic formations through CCS to the cost of SOC sequestration provides insights into how the cost to increase SOC sequestration through NT adoption compares to another potential mechanisms to reduce CO2 emissions. The estimated CO2 storage potential in geologic formations is substantial, over 8300 billion metric tons in saline formations [51], however, little literature is available that provides estimates for the costs to capture, transport, inject, and store CO2 from coal fired power plants, a primary source of CO2 emissions.

The IPCC [22] estimated cost of CO2 capture with geologic storage ranged from $30 to $71 Mg−1 CO2 (adjusted for this analysis from 2005 to 2014 dollars to be $36.36 to $86.06 Mg−1 CO2). These estimates are within the range of other cost estimates [2, 9, 15, 20, 32, 40]). The cost of CO2 avoidance is considered the average cost to reduce CO2 emissions by one unit while providing the same amount of electricity as the reference plant (IPCC [22]).

The marginal cost curve for the CO2 sequestered through NT adoption is compared to the range of costs estimated for geologic storage of CO2 in Fig. 6. Up to 89 Tg CO2 year−1 could be sequestered through NT adoption at a cost that is less than the lowest estimated average cost for geologic storage. Compared to the higher estimated cost to store CO2 in geologic formations, up to 130 Tg CO2 year−1 could be stored on cropland for a lower cost. These results indicate that terrestrial CO2 sequestration on some cropland represents a lower cost alternative to capturing and storing the CO2 in geologic formations.

Fig. 6
figure 6

Marginal cost curve for all tillage sequences on cropland that were converted to NT and estimated low and high geologic storage cost ($36.36–$86.06) to capture at a power plant, transport and store CO2 in geologic formations (CO2 storage cost is converted from $2005 to $2014)

Transitions of historic tillage use to NT influences the effectiveness of NT to increase SOC sequestration. The tillage sequence CTCTNT could capture about 1502 Tg CO2 (75.1 Tg CO2 year−1 for 20 years), which is 84 percent of the potential CO2 sequestration in U.S. cropland soil (1780 Tg CO2) that could be achieved for less than $36.36 Mg−1 CO2 over 20 years (Table 3). The additional 9 Tg CO2 year−1 provided by activities that were not in crops initially but were converted to cropland under CT before moving to NT (tillage sequence NCCTNT) provided enough additional SOC sequestration that the two activities alone could account for 94.4 percent of the potential SOC sequestration on U.S. cropland for a marginal cost lower than the lowest estimated costs for geologic CO2 storage. When the high marginal cost of geologic CO2 storage was considered, activities that were under the tillage sequence of CTRTNT become the second highest contributor of SOC sequestration by adding 19.1 Tg CO2 year−1 and, when combined with cropland under tillage sequences CTCTNT and NCCTNT, accounted for over 97 percent of the potential SOC sequestration at that cost. At a cost of less than $86.06 Mg−1 CO2, these three activities also account for just over 90 percent of the estimated SOC sequestration potential increase on all cropland through NT adoption.

Table 3 SOC sequestration to 30 cm depth by tillage sequence relative to expected cost for geologic CO2 storage

Geologic CO2 storage potential is much larger than SOC sequestration increases estimated here, could continue beyond the twenty-years when SOC achieves a new equilibrium, and the risk of CO2 release may be lower. It is most likely, however, that the portfolio of options needed to address atmospheric CO2 levels will include both, so a comparison of costs provides valuable information.

As described by González-Ramírez et al. [17], SOC sequestration faces the challenges of additionality, ensuring an appropriate baseline, leakage, uncertainty, permanence, monitoring and verification, and distributional effects–such as an impact on crop prices from changes in crop production. Additionality requires that the activities account for increased SOC sequestration that would not have otherwise occurred, or that some landowners would make changes without any payment. In the research presented here, without payment for adopting NT to increase SOC sequestration, about 9.8 Mha or 7.8 percent of cropland was under long term NT (at least five continuous years) in 1997, according to CTIC data. The baseline applied in this research is well defined as the SOC sequestration based on 1997–2017 land use and management on U.S. cropland. Therefore, the increased SOC stocks that are estimated would not have occurred under a business-as-usual scenario and consequently should satisfy the additionality requirement.

The IPCC [21] assesses the uncertainty of SOC estimates based upon the number of studies and variability of study results (Chapter 4; [21]). The uncertainty of land use factors in temperate regions is 9 to 12 percent, under 15 percent for input factors, and under 10 percent for tillage factors [21]. The permanence of SOC sequestration depends on land management. Some of the SOC stock that was increased through NT may be lost if the soil is disturbed through tillage, for example to capture the benefit of increased prices or if yields are reduced, or other reasons. One mechanism to encourage maintaining NT is to retain a portion of the increase in SOC in a reserve pool to serve as insurance against the possibility that the SOC could be released (e.g., the Chicago Climate Change used 20 percent [7]). In addition, measuring and monitoring costs could decrease the payment that could be received by landowners for increasing NT adoption to enhance CO2 sequestration. Furthermore, SOC accumulation in agricultural soils is slow and heterogenous across and within individual fields, making short term changes in SOC stocks difficult to measure over time. While remote sensing techniques are continuing to develop that may ease the difficulty of measuring and monitoring, they may still be an issue.


This study used published estimates for the cost to adopt NT in the U.S. combined with estimates using IPCC factors of the SOC sequestration increases that can be achieved through NT to derive the marginal costs of increasing SOC through these activities. This research demonstrates that SOC sequestration on U.S. cropland through a change in management to NT can efficiently offset a portion of the CO2 emissions entering the atmosphere at a cost that is comparable to the costs of geologic CO2 storage. The results demonstrate that agricultural soils, while a small sink relative to the large annual emissions from the U.S., could still help mitigate the effects of increased CO2 emissions until activities that store substantially more CO2 can be developed and implemented.

Estimates indicate that nearly 95 percent of the biophysical potential SOC sequestration increase on U.S. cropland (2803 Tg CO2 after 20 years from increases of 140.1 Tg CO2 year−1) could be captured for a cost less than $100 Mg−1 CO2 and 64 to 93 percent could be captured for costs less than the lower and higher estimated cost to capture CO2 for geologic storage ($36.36 to $86.06 Mg−1 CO2). Increasing SOC sequestration on U.S. cropland soils could effectively reduce or offset CO2 emissions until CO2 emissions are drastically reduced or geologic storage costs are reduced through improved technologies, alternative sources of fuel are used for energy, or other technological achievements are implemented.

The value of CO2 (price) will ultimately be a function of the instrument used to encourage or enforce CO2 emission reductions, the costs of other CO2 emission reduction activities, and how much those wishing to reduce emissions would be willing to pay for offsets. Policymakers are still determining whether SOC sequestration could represent a legitimate offset for CO2 emission reductions. In the meantime, CO2 emissions continue to increase globally.


For this analysis, EQIP payments are used to represent the minimum payment required to encourage landowners to adopt NT management. Because EQIP payments capture the costs of implementing multiple conservation practices, not just NT, it should represent a conservative estimate of the cost to adopt NT. The value of increased SOC is then a function of this cost and the amount of SOC increase that results from the decreased soil disturbance. The marginal cost curves that result from NT adoption to increase SOC sequestration on conterminous U.S. cropland were developed for this analysis.

The IPCC developed a method for estimating SOC stock changes to 30 cm based on soil properties, climate, land use, biomass inputs, management activities and other factors, that could be applied using varying levels of detailed input information [23]. The IPCC method was updated with revised factors in 2006 to reflect additional research and improved understanding of SOC sequestration dynamics ([21]; Volume 4, Chapter 5). The land use, tillage, and input factors used to estimate the change in SOC over 20-year inventory periods are fixed and provided in the IPCC literature. The land use factor is determined by the climatic region and how the land was used at the beginning of the inventory (e.g., cropland, set-aside, perennial, etc.). The effect of soil disturbance on SOC is captured by the tillage factor, which varies by the intensity of soil disturbance (CT, RT, and NT), and climate. The input factor accounts for the biomass returned to the soil following crop harvest and varies by the level of input and climatic region [21]. The IPCC approach assumes that SOC achieves equilibrium after 20 years when carbon input is exactly offset by carbon losses, so there is no net change in SOC unless there are additional management or input changes. The IPCC approach and factors have been used to capture the change in SOC that results from transitions of tillage intensity from CT to CT to NT (identified as CTCTNT), from CT to RT to NT (CTRTNT), CT to NT to NT (CTNTNT) etc., with different SOC sequestration rates for each transition and crop rotation [44, 45]. The change in the SOC stock on cropland soils was estimated for this analysis using the 2006 IPCC factors and the approach described by Sperow [44] that traces the transition between crop rotations and tillage intensities through three inventories.

Land use and crop rotations used in this analysis were derived from the 1997 National Resources Inventory (NRI) database which provides data on land use and other activities every 5 years since 1982 [35]. More current data to the same level of detail required for the analysis are not available. Summary NRI data are available for 2007 (USDA-NRCS [59]) and later [54], but these sources do not provide data at the level of detail required for this analysis. Recent NRI reports indicate that there has been little change in the amount of U.S. cropland between 1997 and 2017 (about 2 percent; USDA [53]). Therefore the 20 years of crops grown from the 1982–1997 NRI data applied in the analysis should be adequate for estimating potential SOC sequestration U.S. cropland. The cropping activities addressed in the analysis were derived from the crop rotations established by Eve et al. [14] based upon the predominant crop type (e.g., row crop, small grain, hay, etc.) produced during each 5-year period between NRI surveys (the crop grown in four of the 5 years of data is included in the NRI).

The area of cropland by tillage intensity was derived from data provided by the Conservation Technology Information Center (CTIC) who provided relevant data for tillage intensity by IPCC defined climatic region and crop rotation [14]. Long term (five consecutive years) NT with adequate moisture is necessary in humid and temperate dry climates for NT cropping systems to increase SOC relative to CT [1, 42]. Data for long-term NT adoption provided by the CTIC indicate that, while tillage intensity varies by cropland and climatic region, 1 to 12 percent of U.S. cropland (7.8 Mha total) was under NT in 1997 [14]. A subset of these data show an overall average NT adoption rate of 8.6 percent on the 38 Mha (million hectares) of cropland within the Upper Mississippi River Basin (all or parts of IA, IL, IN, MO, MN, and WI). These data are a little lower than the 13% NT on the smaller area of 4.9 Mha in the Upper Mississippi River Basin [19].

The first inventory addresses the SOC change that results from land use and management activities implemented in 1982. The SOC stock estimates made for 1982 capture the SOC stock at the beginning of the inventory. The first inventory covered from 1982 until 1997. In this analysis, the SOC stock at the beginning of 1997 is the same as the ending stock for the 1982 inventory. If there was no change in land use or management, the SOC stock does not change again and will be zero for the next inventory. Since the IPCC captures the SOC changes between two inventories, the land use and management activities implemented in 1997 were assumed to remain in place until the end of the inventory in 2017.

Potential change in SOC was estimated based on the assumption that the crop rotation in 2017 is the same as the crop rotation and management as at the end of the 1997 inventory. The only change to management was to reduce the level of soil disturbance by adopting NT on all cropland. Land that was already in NT at the end of the 1997 inventory had no additional changes to SOC stocks because there were no additional land use or management changes that alter the SOC stock.

For this analysis, U.S. cropland in 1997 was assessed to determine the potential for increasing the SOC stock through use of NT. All land for which NT adoption was possible was converted to NT for this analysis. Land that was already removed from crop production for the Conservation Reserve Program (CRP) and land that was not managed as cropland (e.g., hay, pasture, etc.) in 1997 were not considered in the analysis because NT could not be applied to them. The NRI data, combined with the IPCC SOC estimation approach, indicate that 124.7 Mha of cropland was used to produce crops in 1997. The CTIC data indicate that there was no cropland managed with NT in 1982, but there was NT cropland in 1997. About 9.8 Mha of cropland was already under NT in 1997, so there was no change in the SOC stock when this cropland continued in NT in 2017. Consequently, only the remaining 114.9 Mha of cropland in the analysis could be converted from a more intensive soil disturbance management system (either CT or RT) to NT.

Cost to increase NT adoption–EQIP payment data.

EQIP payment data were collected for each U.S. state individually [56, 58] and through the county data provided by USDA-NRCS [57]. EQIP provides for annual payments for up to ten years and NT needs to be maintained for one year for landowners to receive EQIP payments [55]. All of the expected costs of incorporating NT into farm management activities are covered by the EQIP payment, including material, equipment, knowledge accumulation (in some cases), and labor. EQIP payments vary across states but do not vary within a state. For all U.S. states, payments for NT adoption range from $18.29 to $125.73 ha−1 (Fig. 5), with an overall average cost share payment of $53.23 ha−1.

The highest EQIP payments (greater than $100 ha−1) are in the northwest (WA), south (TX) northeast (NH), and the High Plains (WY), each with very different climatic conditions and soil characteristics. It is interesting to note that landowner costs are estimated to be $133.58 ha−1 in WA but only $20.95 ha−1 in OR, an adjacent state. For landowners in most states, the expected costs of adopting NT vary from $40 to $80 ha−1. These costs are higher than estimated by Stonehouse and Bohl [48], yet even though landowner costs would be covered by the EQIP payments, there is still little adoption of NT.

Perceived risk is frequently cited as a reason for the limited adoption of NT in the U.S. [24]. Published EQIP payment schedules indicate that states generally either identify the risk of conservation tillage activities as zero explicitly (LA and TX), or do not include any information about risk (45 states). Colorado is the only state to include an estimate of the increased risk from a change in residue management.

Estimating marginal costs.

For this analysis, the carbon value is a function of the amount of SOC that can be stored per ha and the state level EQIP payment that was offered to landowners to change from a CT to NT. The EQIP rules for length of payment and requirements for maintaining the practice are not applied because the data are only used to estimate of the cost to change from CT to NT. Most studies present the value of stored carbon in terms of CO2. Since SOC is potential CO2 in the atmosphere [36], SOC (Mg C ha−1 year−1) is converted to mass of CO2 (Mg CO2 ha−1 year−1) based upon the relative masses (i.e., mass of a CO2 molecule to mass of C molecule) by multiplying SOC by 44/12.

The carbon value was estimated as the cost to the landowner of implementing NT (EQIP payment) divided by the carbon sequestration rate (Mg CO2 ha−1 year−1) achieved by adopting no-till using Eq. 1.

$$C_{{value}} \; = \;\frac{{EQIP\;Payment\;(\$ \;ha^{{ - 1}} )}}{{MgCO_{2} \;ha^{{ - 1}} \;year^{{ - 1}} }}.$$

Availability of data and materials

Only summary NRI data are available summary data available at, Climate data: EQIP data:



Conventional tillage




Reduced tillage


Conservation technology information center


Conventional tillage, conventional tillage, no-tillage sequence


Conventional tillage, reduced tillage, no-tillage sequence


Conventional tillage, no-tillage, no-tillage sequence


Non-cropland, conventional tillage, no-tillage sequence


Reduced tillage, conventional tillage, no-tillage sequence


Non-cropland (grass, pasture, or some other land-use)


Environmental quality incentives program


Intergovernmental panel on climate change


National Resources Inventory


Soil organic carbon


  1. Abreu SL, Godsey CB, Edwards JT, Warren JG. Assessing carbon and nitrogen stocks of no-till systems in Oklahoma. Soil Tillage Res. 2011;117:28–33.

    Article  Google Scholar 

  2. Antle J, Valdiva R, Capalbo S. Economic analysis of CO2 sequestration, utilization, and storage. Presentation to the Big Sky Carbon Sequestration Partnership Annual Meeting. Great Falls 2012.

  3. Antle JM, Capalbo SM, Paustian K, Kamar Ali M. Estimating the economic potential for agricultural soil carbon sequestration in the Central United States using an aggregate econometric-process simulation model. Clim Change. 2007;80:145–71.

    Article  CAS  Google Scholar 

  4. Biardeau, L., R. Crebbin-Coates, R. Keerati, S. Litke, and H. Rodriguez. 2016. Soil health and carbon sequestration in US croplands: a policy analysis. Accessed 2 Sept 2020.

  5. Bruce JP, Frome M, Haites E, Janzen H, Lal R, Paustian K. Carbon sequestration in soils. J Soil Water Conservat. 1999;54:382–9.

    Google Scholar 

  6. Claassen R, Bowman M, McFadden J, Smith D, Wallander S. 2018. Tillage Intensity and Conservation Cropping in the United States, EIB-197, U.S. Department of Agriculture, Economic Research Service, 2018.

  7. CCX. 2008. Soil Carbon Management Offsets. (Chicago Climate Exchange Brochure), Accessed 24 March 2016.

  8. Cole CV, Flach K, Lee J, Sauerbeck D, Stewart B. Agricultural sources and sinks of carbon. Water Air Pollution. 1993;70:111–22.

    Article  CAS  Google Scholar 

  9. Dahowski RT, Li X, Davidson CL, Wei J, Dooley J, Gentile RH. Regional opportunities for carbon dioxide capture and storage in China. Department of Energy publication. PNNL-SA-68786. 2009.

  10. Diagana B, Antle J, Stoorvogel J, Gray K. Economic potential for soil carbon sequestration in the Nioro region of Senegal’s Peanut Basin. Agr Syst. 2007;94:26–7.

    Article  Google Scholar 

  11. Doraiswamy PC, McCarty GW, Hunt ER Jr, Yost RS, Doumbia M, Franzluebbers AJ. Modeling soil carbon sequestration in agricultural lands of Mali. Agr Syst. 2007;94:63–74.

    Article  Google Scholar 

  12. EPA (U.S. Environmental Protection Agency), 2019a. Greenhouse Gas Emissions Data. Accessed 30 Nov 2019.

  13. EPA (U.S. Environmental Protection Agency). Inventory of U.S. Greenhouse Gas Emissions and Sinks: 1990–2017. Washington, DC. 2019.

  14. Eve MD, Paustian K, Follett R, Elliot ET. A national inventory of changes in soil C from National Resources Inventory Data. In: Lal R, Kimble JM, Follett RF, Stewart BA, editors. Assessment Methods for Soil C. Boca Raton: Lewis Publishers; 2001. p. 593–610.

    Google Scholar 

  15. Finkernath M. Cost and performance of carbon dioxide capture from power generation. International Energy Agency Working Paper. 2011. Accessed 1 May 2015.

  16. Global CCS Institute. 2019. The Global Status of CCS. Australia. Accessed 17 Nov 2020.

  17. González-Ramírez J, Kling CL, Valcu A. An overview of carbon offsets from agriculture. Ann Rev Resour Econ. 2012;4:145–60.

    Article  Google Scholar 

  18. Grace PR, Antle J, Aggarwal PK, Ogle S, Paustian K, Basso B (2012) Soil carbon sequestration and associated economic costs for farming systems of the Indo-Gangetic Plain: a meta-analysis. Agri Ecosyst Environ 146(1):137–146

  19. Horowitz J, Ebel R, Ueda K. “No-Till” Farming is a growing practice. USDA-ERS Bulletin Number 70. 2010.

  20. IEA (International Energy Agency). CO2 capture and storage A key carbon abatement option. Paris: OECD/IEA; 2008.

    Book  Google Scholar 

  21. IPCC. 2006. 2006 IPCC Guidelines for national greenhouse gas inventories, prepared by the National Greenhouse Gas Inventories Programme, Eggleston H.S., Buendia L., Miwa K., Ngara T. and Tanabe K. (eds). Published: IGES, Japan.

  22. IPCC. 2005: IPCC Special report on carbon dioxide capture and storage. Prepared by Working Group III of the Intergovernmental Panel on Climate Change [Metz, B., O. Davidson, H. C. de Coninck, M. Loos, and L. A. Meyer (eds.)]. Cambridge University Press, Cambridge, United Kingdom and New York, 442 pp.

  23. IPCC. 1997. Revised 1996 IPCC guidelines for national greenhouse gas inventories reporting instructions (Volume 1), In: Houghton JT, Meria Filho LG, Lim B, Treanton K, Mamaty I, Bonduki Y, Griggs DJ, Callender BA (eds.), Intergovernmental Panel on Climate Change.

  24. Knowler D, Bradshaw B. Farmer’s adoption of conservation agriculture: a review and synthesis of recent research. Food Policy. 2007;32:25–48.

    Article  Google Scholar 

  25. Lal R, Follett RF, Kimble J, Cole CV. Managing U.S. Cropland to Sequester Carbon in Soil. J Soil Water Conserv. 1999;54:374–81.

    Google Scholar 

  26. Lal R, Kimble J, Follett RF, Cole CV. The Potential for U.S Cropland to Sequester Carbon and Mitigate the Greenhouse Effect. Ann Arbor: Sleeping Bear Press; 1998. p. 128.

    Google Scholar 

  27. Lal R, Reicosky DC, Hanson JD. Evolution of the plow over 10,000 years and the rationale for no-till farming. Soil Tillage Res. 2007; 1–12.

  28. Lam SK, Chen D, Mosier AR, Rousch R. The potential for carbon sequestration in Australian agricultural soils is technically and economically limited. Sci Rep. 2013;3:2179.

    Article  Google Scholar 

  29. Lewandrowski J, Peters M, Jones C, House R, Sperow M, Eve M, Paustian K. Economics of sequestering carbon in the US agricultural sector. USDA-ERS Technical Bulletin Number 1909, Washington, DC. 2004

  30. McCarl B, Schneider U. Greenhouse gas mitigation in US agriculture and forestry. Science. 2001;294:S2481–2.

    Article  Google Scholar 

  31. McKinsey & Co. 2009. Pathways to a Low-Carbon Economy. Version 2 of the Global Greenhouse Gas Abatement Cost Curve. McKinsey & Co. Accessed 05 Nov 2016.

  32. Merkel TC, Lin H, Wei X, Baker R. Power plant post-combustion carbon dioxide capture: An opportunity for membranes. J Membr Sci. 2010;359:126–39.

    Article  CAS  Google Scholar 

  33. Nielsen ASE, Plantinga AJ, Alig RJ. 2014. New cost estimates for Carbon sequestration through afforestation in the United States. USDA Forest Service General Technical Report PNW-GTR-888. 2014.

  34. NOAA (National Oceanic & Atmospheric Administration). Earth System Research Laboratory, Global Monitoring Division. 2019. Accessed 28 Dec 2019.

  35. Nusser SM, Goebel JJ. The National Resources Inventory a long-term multi-resource monitoring programme. Environ Ecol Stat. 1997;4:181–204.

    Article  Google Scholar 

  36. Patton D, Bergstrom JC, Moore R, Covich AP. Economic value of carbon storage in U.S. National Wildlife Refuge wetland ecosystems. Ecosyst Serv. 2015;16:94–104.

    Article  Google Scholar 

  37. Paustian K, Andren O, Janzen HH, Lal R, Smith P, Tian G, Tiessen H, Van Noorwijk M, Woomer PL. Agricultural soils as a sink to mitigate CO2 emissions. Soil Use Manag. 1997;13:230–44.

    Article  Google Scholar 

  38. Paustian K, Collins HP, Paul EA. Management controls on soil carbon. In: Paul EA, Paustian K, Elliot ET, Cole CV, editors. Soil Organic Matter in Temperate Agroecosystems: Long-Term Experiments in North America. Boca Raton: CRC Press; 1997. p. 15–49.

    Google Scholar 

  39. PRISM Climate Group, Oregon State University,, Accessed 19 Mar 2014.

  40. Rubin ES, Chen C, Rao AB. Cost and performance of fossil fuel power plants with CO2 capture and storage. Energy Policy. 2007;35:4444–54.

    Article  Google Scholar 

  41. Shapiro CA, Holshouser DL, Kranz WL, Shelton DP, Witkowski JF, Jarvi KJ. Tillage and management alternatives for returning conservation reserve program land to crops. Agron J. 2001;93:850–62.

    Article  Google Scholar 

  42. Six J, Ogle SM, Breidt FJ, Conant RT, Mosiers AR, Paustian K. The potential to mitigate global warming with no-tillage management in only realized when practiced on the long-term. Glob Change Biol. 2004;10:155–60.

    Article  Google Scholar 

  43. Sperow, M. 2019. Marginal cost to increase soil organic carbon using no-till on U.S. cropland. Mitigation and Adaptation Strategies for Global Change, 24:93–112

  44. Sperow M. Estimating soil carbon sequestration potential on U.S. agricultural topsoils. Soil Tillage Res. 2016;155:390–400.

    Article  Google Scholar 

  45. Sperow M. An enhanced method for using the IPCC approach to estimate soil carbon storage potential on U.S. agricultural soils. Agr Ecosyst Environ. 2014;193:96–107.

    Article  CAS  Google Scholar 

  46. Sperow M, Eve M, Paustian K. Potential soil C Sequestration on U.S. agricultural soils. Clim Change. 2003;57:319–39.

    Article  CAS  Google Scholar 

  47. Sperow M, House RM, Paustian K, Peters M.Economic Feasibility of Soil C Sequestration in US Agricultural Soils. In: Kimble J, Lal R, Follett R (Eds) Agriculture Practices and Policies for Carbon Sequestration in Soil Lewis Publishers, Boca Raton, FL 2002, pp 337–348.

  48. Stonehouse DP, Bohl MJ. Selected government policies for encouraging soil conservation on Ontario cash-cropping farms. J Soil Water Conserv. 1993;48(4):343–9.

    Google Scholar 

  49. Toliver DK, Larson JA, Roberts RK, English BC, De La Torre Ugarte DG, West TO. Effects of no-till on yields as influenced by crop and environmental factors. Agron J. 2012;104(2):530–41.

    Article  Google Scholar 

  50. Towery D, Werblow S. Facilitating conservation farming practices and enhancing environmental sustainability with agricultural biotechnology. The Conservation Technology Information Center, West Lafayette, IN, USA. 2010. Accessed 6 Feb 2013.

  51. USDOE (U.S. Department of Energy). U.S. Carbon Storage Atlas, Fifth Edition. 2015. Accessed 17 Nov 2020.

  52. USDA-ERS. 2000. Farm Resource Regions, Agricultural Information Bulletin Number 760,, Accessed 6 April 2016.

  53. USDA-NRCS. Summary Report: 2017 National Resources Inventory, Natural Resources Conservation Service, Washington, DC, and Center for Survey Statistics and Methodology, Iowa State University, Ames, Iowa. 2020.

  54. USDA-NRCS. 2015. Summary Report. National Resources Inventory, Natural Resources Conservation Service, Washington, DC, and Center for Survey Statistics and Methodology, Iowa State University, Ames, Iowa. 2012.

  55. USDA-NRCS. Environmental Quality Incentives Program. 2014a. 19 Feb 2014.

  56. USDA-NRCS. Environmental Quality Incentives Program. 2014b., Accessed 19 Feb 2014.

  57. USDA-NRCS. FOTG (Field Office Technical Guide) County Locator. 2014c. Accessed 19 Feb 2014.

  58. USDA-NRCS. Financial Management Modernization Initiative (FMMI) November 2014; Foundation Financial Information System (FFIS) December 2011. ProTracts Program Contracts System October 2014; National Conservation Planning Database November 2014; Natural Resources Conservation Service, Washington, DC. 2014d. Accessed 15 Jan 2016

  59. USDA-NRCS. Summary Report: 2007 National Resources Inventory, Natural Resources Conservation Service, Washington, DC, and Center for Survey Statistics and Methodology, Iowa State University, Ames, Iowa. 123 pages. 2009.

  60. Wade T, Claassen R, Wallander S. Conservation-Practice Adoption Rates Vary Widely by Crop and Region, EIB-147, U.S. Department of Agriculture, Economic Research Service. 2015.

  61. Wilhelm WW, Wortmann CS. Tillage and rotation interactions for corn and soybean grain yield as affected by precipitation and air temperature. Agron J. 2004;96:425–32.

    Article  Google Scholar 

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Scientific Article No. 3383 of the West Virginia Agricultural and Forestry Experiment Station, Morgantown, WV.


Funding for this research was partially provided by a grant from the United States Department of Agriculture, Economic Research Service and the West Virginia Agricultural and Forestry Experiment Station.

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MS conceived and designed the research, collected the data used for the analysis, developed the model code, analyzed the data, and wrote the paper.The author read and approved the final manuscript.

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Sperow, M. What might it cost to increase soil organic carbon using no-till on U.S. cropland?. Carbon Balance Manage 15, 26 (2020).

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