SN Applied Sciences

, 1:1662 | Cite as

Characterization of atmospheric nitrous oxide emissions from global agricultural soils

  • Viney P. AnejaEmail author
  • William H. Schlesinger
  • Qi Li
  • Alberth Nahas
  • William H. Battye
Research Article
Part of the following topical collections:
  1. 2. Earth and Environmental Sciences (general)


Nitrous oxide (N2O) is a potent greenhouse gas with an atmospheric lifetime of ~ 114 years. Agriculture activities are the main sources for N2O emission into the atmosphere by human activities. Global N2O emissions into the atmosphere are projected to increase in the coming years as demand for food, fibre and energy increases owing to increasing global population. Here, a statistical model (N2O_STAT) is developed for characterizing atmospheric N2O emissions from agricultural sources. We obtained N2O emissions and physicochemical variables (i.e. air temperature, soil temperature, soil moisture, soil pH, and N input to the soil) from published journal articles since 2000. A statistical model was developed by expressing a multiple linear regression equation between N2O emission and the physicochemical variables. The model was evaluated for 2012 N2O emissions. Results of the model are compared with other global and regional N2O models (e.g. EDGAR, EPA/USGS, and FAOSTAT). In comparison with other data sets, the model generates a lower global N2O estimate by 9–20% (N2O_STAT: 3.75 Tg N yr−1; EDGAR: 4.49 Tg N yr−1; FAO: 4.07 Tg N yr−1), but is ~ 25% higher when compared to Bouwman et al. (Glob Biogeochem Cycles 16:1–9., 2002) (2.80 Tg N yr−1). We also performed a region-based analysis (USA, India, and China) using the N2O_STAT model. For the USA, our model produces an estimate that ranges from − 13 to + 32% in comparison with other published data sets. Meanwhile, the N2O_STAT model estimate for India shows N2O emissions between − 56 and + 14% when compared to other data sets. A much lower estimate is seen for China, where the model estimates N2O emissions 38–177% lower than other data sets. The N2O_STAT model provides an opportunity to predict future N2O emissions in a changing world.


Nitrous oxide Emissions Agricultural soil Statistical model 

1 Introduction

The largest human influence on climate since the end of the twentieth century is the emission of greenhouse gases to the atmosphere. In addition to carbon dioxide (CO2), nitrous oxide (N2O) is one of the most important greenhouse gases that has a global warming potential (GWP) of ~ 300 for a 100-year timescale [1]. N2O also contributes to the destruction of ozone in the stratosphere [2]. The lifetime of N2O in the atmosphere is ~ 114 years, indicating its long-term influence on a planetary scale [3].

Since 1978, globally averaged N2O concentrations in the atmosphere have been measured at Mauna Loa, Hawaii. Prior to 1978, N2O levels were extracted from ice cores from Antarctica. N2O concentrations in the atmosphere were relatively stable until the start of the Industrial Revolution [4]. Since that time, N2O concentration has increased by 18%, from ~ 270 ppb to the current value of ~ 331 ppb (Fig. 1). This increase is primarily due to intensive human activities, particularly related to agriculture.
Fig. 1

Atmospheric N2O concentration trend from the combined Global Monitoring Division data set for the period 1977–2018 [33]

Ciais et al. [5] have estimated the yearly emission of N2O to be 17.9 Tg N yr−1 for the period 2006–2011. N2O emissions from natural sources are 11.0 Tg N yr−1, which includes sources from land and oceans. Agricultural activities are the primary anthropogenic source of N2O, contributing to 5.6 Tg N yr−1 [6]. With increasing food, fibre and energy production, along with climate change and agricultural intensification, N2O emissions from soils have increased since 1990, from 3.5 Tg N yr−1 to 4.1 Tg N yr−1 [7].

During the period 1961–2010, global N2O emissions from manure usage have grown from 1.17 to 2.03 Tg N yr−1 at an average rate of 1.10% yr−1 [8]. Meanwhile during the same period, N2O emissions from synthetic fertilizers have increased from 0.14 to 1.40 Tg N yr−1 at an average rate of 3.90% yr−1 globally [9]. This indicates that synthetic fertilizers will have a greater contribution to N2O emission than manure within less than 10 years [8]. Besides agriculture, other sources such as fossil fuel combustion, industrial processes, and biomass burning also contribute to the total N2O emissions, but these are all relatively small sources.

Intensive fertilizer use has increased the emissions of reactive nitrogen compounds, including N2O from soils through nitrification and denitrification processes (Supplementary Figure 1S). Nitrification is the aerobic microbial oxidation of ammonium or ammonia to nitrite followed by oxidation of nitrite to nitrate. It is an important process in the nitrogen cycle in which N2O is generated as a by-product that leaks from microbial cells into soil and eventually into the atmosphere [6]. Denitrification is a microbially facilitated process that leads to significant N losses from agricultural systems. Through denitrification, nitrate and nitrite are reduced, and a portion converted into N2O [10].

The ratios of N2O/NO3 (nitrification) to N2O/N2 (denitrification) products are important parameters determining the change of global budget, and they are affected by various physical, chemical and biological factors and their interacting effects [11]. To develop a predictive model for N2O emission under different agroecosystems, climate variables, soil characteristics, and cropping practices must be considered. Granli and Bockman [11] provided a review of the factors that control N2O emissions from soil, including moisture and aeration, temperature, soluble and decomposable carbon, soil and fertilizer nitrogen, soil pH and salinity. Table 1 summarizes the variables that affect product ratios during nitrification and denitrification in agricultural soils. In nitrification, N2O emission will increase with decreasing O2 concentration, increasing water above field capacity, low NH4+ concentrations, deviations of pH from near neutrality, and increasing temperature. The production of N2O by denitrification is enhanced in conditions characterized by high nitrate, high C availability, low pH, high temperature, low N2O reductase activity, and 60–90% water-filled pore space (WFPS) [12, 13, 14].
Table 1

Variables that affect product ratios during nitrification and denitrification in agricultural soils

[11, 34]





Will increase N2O/NO3 ratio



Decreasing O2 concentration



Increasing H2O above field capacity



Low NH4+ concentrations



Increasing or decreasing pH



Increasing temperature


Will increase N2O/N2 ratio


[NO3] or [NO2]

Increasing oxidant



Increasing O2



Decreasing C availability



Decreasing pH



Decreasing temperature


Enzyme status

Low N2O reductase activity



Decreasing between 60 and 90% WFPS

Uncertainties of estimates of sources and sinks still exist in global N2O budget, especially from agricultural soils [15]. Inadequate understanding of the mechanisms controlling N2O emission from agricultural soils may be responsible for limited attention to agriculture as a major contributor of the increasing atmospheric N2O. With increasing food and energy production, along with climate change and agricultural intensification, N2O emissions from soils and groundwater are likely to increase, indicating the need for an updated global budget for N2O that accounts for these recent changes.

The goal of this project is to develop a statistical model to predict N2O emissions from agricultural soils containing synthetic and organic fertilizers using physicochemical properties of the system from different regions. We also analyse the spatial distribution of N2O emissions from agricultural soils and compare the results with other modelled emission inventories (i.e. EDGAR v.4.3.2, EPA, and FAOSTAT).

2 Methodology

Based on literature review, we found four variables of importance in controlling N2O emissions from soil: (1) soil moisture, (2) soil and air temperature, (3) synthetic and organic fertilizer usage, and (4) soil pH [16]. The highest N2O emissions are usually due to high temperature and ample precipitation because increasing soil temperature stimulates microbial activities related to nitrification and denitrification. We performed a series of statistical analyses utilizing the RStudio statistical software ( to examine the distribution of data and to fit an appropriate regression model with N2O as the response (dependent) variable and other variables as independent predictors. We then used Integrated Land and Water Information System (ILWIS) v.3.31 Academic (, a GIS tool to prepare the global data sets and apply the statistical model to predict N2O emissions.

2.1 Data collection

Data collection includes two parts: (1) data sets for developing the statistical model (Table 2) and (2) global data sets for extrapolating the results to larger areas (Table 3). For the statistical model, we conducted a literature review regarding agricultural soil N2O emission (published after 2000). Data were derived from two sources: (1) field data for developing the statistical model and (2) global data for extrapolating the results to larger areas. The complete data set is compiled in Supplementary Table 1S.
Table 2

Data for statistical model development



N2O emissions

kg N ha−1 year−1

Air temperature


Soil temperature


Soil pH

Soil moisture


Fertilizer N content usage

kg N ha−1 year−1

Manure N content usage

kg N ha−1 year−1

Table 3

Global data set used for prediction


Data sets

Soil temperature; soil pH

Harmonized World Soil Database v 1.2

Soil moisture

The Global Soil Dataset for Earth System Modeling

Air temperature

ERA-Interim Global Atmospheric Reanalysis

Cropland cover, fertilizer usage, manure usage

EarthStat’s Cropland and Pasture Area (with modification)

2.2 Model development

Based on the statistical analysis, we found that the data distribution, shown as the histogram of N2O emissions (Fig. 2a), was skewed to the right. To normalize the data, we transformed them to logarithmic values (Fig. 2b), which were normally distributed. Then, we used a multiple linear regression model to fit the response variable (the log of N2O emissions), using the physicochemical variables as predictors. The statistically derived model (hereinafter N2O_STAT) to predict N2O emissions from agricultural soils is mathematically expressed as the following:
$${\text{N}}_{2} {\text{O}}\,{\text{emission}} = \left( {\exp \left[ {A + B \times T_{\text{soil}} + C \times {\text{SM}} + D \times {\text{pH}}_{\text{soil}} + E \times {\text{N}}\,{\text{input}} + F \times {\text{Fertilizer}}\,{\text{type}}} \right]} \right) \times \frac{28}{44}$$
where Tsoil refers to soil temperature (°C), SM soil moisture (%), and the coefficients A, B, C, D, E, and F are statistically derived parameters (Table 4). N input is differentiated by synthetic or organic fertilizer and is expressed as kg N ha−1 yr−1. The units for predicted N2O emission are kg N ha−1 yr−1. Initially, air temperature was included as a variable in the model, but it was later omitted from the equation because it had an insignificant correlation with N2O emission.
Fig. 2

a Histogram of N2O emission and b log of N2O emission

Table 4

Summary of the statistical model




p value






Soil temperature




Soil moisture




Soil pH

− 0.3454



Nitrogen input




Fertilizer type



Table 4 summarizes the coefficients and p values of each variable. The residual standard error is 0.928, and R-squared is 0.2. The F test shows that this multivariate linear regression model is statistically significant at 90% confidence level. Based on the p value, the soil moisture, soil pH, and fertilizer type are statistically significant. Notably, the magnitude of nitrogen input does not have a significant influence on the N2O emission rate. This may seem counterintuitive, but N2O emissions are produced by nitrification and denitrification, and nitrogen concentrations may be the limiting factor for these reactions only when the levels of soil nitrogen are low. Other factors are likely to be limiting when soil nitrogen concentrations are at agronomic levels [6]. Yu and Zhuang [16] corroborate these findings using their trait-based biogeochemistry model to estimate global N2O emissions that were more sensitive to temperature and precipitation and less sensitive to soil organic carbon and nitrogen contents.

2.3 Model diagnostics

After running the regression analysis, we verified that N2O_STAT works well for fitting the data and complies with the assumptions of linear regression models. A two-step model diagnostic was performed by analysing the variance and distribution of the residuals (Supplementary Figure 2S). The equal distribution with no distinct patterns of residuals around the horizontal provides a good indication of the likelihood of a linear relationship. Additionally, the residuals are well fitted on the straight line, indicating that the data are indeed normally distributed. The outliers indicated by residuals that are far from the line were excluded in further analysis.

We tested different model forms, i.e. linear form (classical emission factor approach) and exponential form (this study). The exponential form had r2 = 0.2, and residual standard error = 0.93, which are better than in the linear model (r2 = 0.14 and residual standard error = 1.02), suggesting that the exponential model is preferred in modelling the N2O emission.

2.4 Other N2O emission inventories

2.4.1 EDGAR

The Emission Database for Global Atmospheric Research compiles anthropogenic global N2O emissions and trends from 1970 to 2012 based on international statistics and emission factors [17]. N2O emissions from fertilizer are based on the estimation from the International Fertilizer Industry Association (IFA) and the Food and Agriculture Organization Statistics Division (FAOSTAT). The N2O emission factor for direct soil emissions from the use of synthetic fertilizer and from manure and from crop residues is based on IPCC Guideline [7]. For the comparison purposes, we use the 2012 global N2O data set for agricultural soils (subsector 4C + 4D).

2.4.2 EPA greenhouse gas inventory report and USGS county-level data sets

We calculated N2O emission from agriculture soils over the continental USA based on subsectors described in the EPA report [18]. The subsector emissions are taken from the county-level information compiled by USGS from the 2012 census of agriculture [19, 20]. The county-level information consists of fertilizer usage, manure applications, and crop residue. Then we calculated the emissions which are interpolated to generate a spatial distribution of the emission for the USA.

2.4.3 FAOSTAT (

Food and Agriculture Organization of the United Nations develops methods and standards for food and agriculture statistics, provides technical assistance services, and disseminates data for global monitoring. It provides the N2O global emissions from synthetic fertilizers, manure applied to soils, manure left on pasture, and crop residues in 2012.

3 Results

3.1 Global

After calculating the coefficients for all variables, we applied the N2O_STAT model for each grid cell and generated a global map for N2O emissions. Figure 3a gives the spatial distribution of global N2O emission from agricultural soils calculated using N2O_STAT in kg Nyr−1 grid cell−1. The resolution of this map is 5 arc-minute by 5 arc-minute, which is equivalent to 8464 ha. The average N2O emission from agricultural soils is ~ 9000 kg N yr−1 grid cell−1, which is comparable to average values of 1 kg ha−1 for agricultural soils, reported by Kim et al. [21] and Shcherbak et al. [22].
Fig. 3

Comparison between the results from a N2O_STAT, b EDGAR, and c absolute difference between the two models (in ton N2O yr−1 grid cell−1). The maps are generated using ILWIS v3.8.5 (

Figure 3b shows spatial distribution of global N2O emission from agricultural soil based on EDGAR. Total annual global N2O emissions from N2O_STAT and EDGAR are 3.75 Tg N yr−1 and 4.49 Tg N yr−1, respectively. It is encouraging to see that, in general, the model captures the global spatial pattern in N2O emissions well. Figure 3c shows the absolute difference between N2O_STAT and EDGAR. In comparison with EDGAR, N2O_STAT gives lower N2O emission values in North America, South America, India, and China, while higher values in Eastern Europe and mid-Africa.

3.2 Continental USA, India, and China

Figure 4 provides the comparison between the results from N2O_STAT, EDGAR, and EPA/USGS over the continental USA (hereafter listed as USA). Total N2O emissions from agricultural soils in the USA calculated from N2O_STAT, EDGAR, and EPA/USGS are 0.35 Tg N yr−1, 0.43 Tg N yr−1, and 0.46 Tg N yr−1, respectively. N2O_STAT performs well in capturing the spatial pattern and the total annual emission. Figure 5 gives the absolute difference of N2O emissions between N2O_STAT model and EDGAR and between N2O_STAT and EPA/USGS. Based on Fig. 5a, N2O_STAT underestimates N2O emission in the Midwest region of the USA and overestimates emissions in the south-eastern region, compared with EDGAR. Figure 5b shows that N2O_STAT gives lower N2O emission values in northern Texas, California, Florida, and states around Lake Michigan, while in other areas the values are comparable to EPA/USGS.
Fig. 4

Comparison between the results from a N2O_STAT, b EDGAR, and c EPA/USGS (in ton N2O yr−1 grid cell−1). The maps are generated using ILWIS v3.8.5 (

Fig. 5

Absolute difference of N2O emissions over CONUS between a N2O_STAT and EDGAR, b between N2O_STAT and EPA/USGS (in ton N2O yr−1 grid cell−1). The maps are generated using ILWIS v3.8.5 (

Figure 6 and Table 5 show close agreement with the N2O_STAT estimate of agricultural soil emissions for India when compared with EDGAR (~ − 14%), the finely resolved N2O emission estimate by Aneja et al. [23] (~ 17%), and FAOSTAT (~ − 7%). Moreover, Table 5 compares the finely resolved N2O emission for India with other published studies. The Aneja et al. [23] results are higher than the results of Garg et al. [24] and Sharma et al. [25], perhaps due to the selection of higher emission factors by Aneja et al. [23]. Overall, we believe that Aneja et al. [23] is more appropriate because these researchers used the activity-level data at district levels and chose the emission factors suitable for Asian context.
Fig. 6

Comparison between the results from a N2O_STAT, b EDGAR, and c the absolute difference between N2O_STAT and EDGAR (in ton N2O yr−1 grid cell−1). The maps are generated using ILWIS v3.8.5 (

Table 5

Summary of N2O emission from different inventories

Emission inventory

N2O (Tg N yr−1)




















Bouwman et al. [32]




EPA Report


Aneja et al. [23]


Garg et al. [24]


Sharma et al. [25]


Gao et al. [26]


Zhou et al. [27]


Meanwhile for China, our estimate using N2O_STAT is 2.3–2.8 times lower than those estimated by EDGAR and FAO. Our N2O emission estimate, however, is in good agreement with Gao et al. [26] and Zhou et al. [27] being 2% higher and 38% lower, respectively. These two studies employ different methods in estimating N2O emission from Chinese agricultural soils. Gao et al. [26] studied N2O direct emissions from croplands by using localized emission factors, while Zhou et al. [27], in addition to using regional emission factors, utilized high-resolution activity data and localized parameters.

4 Discussion

We have developed a novel way to approach global nitrous oxide emissions from agricultural soils (N2O_STAT). We have also used three case studies (USA, India, and China) to strengthen our model development. Unlike all previous N2O emission studies, our approach relies on global emission measurements rather than emission factors and activity data.

Table 5 summarizes the data comparison between N2O_STAT, EDGAR, EPA/USGS, and FAOSTAT for N2O emission from agricultural soils for the USA, India, China, and globally. The FAOSTAT, EDGAR, and EPA estimates are slightly different, although consistent given the large uncertainties in the IPCC default methodologies [9]. Tubiello et al. [9] compared N2O emission from four databases. The results show that the EPA 2006 and EPA 2011 provided the highest values, while FAOSTAT gave the lowest, consistent with our study.

In developing N2O_STAT, we collected data for published N2O emissions that correspond to the use of fertilizer and manure on particular soils (Supplementary Table 1S). N2O_STAT, however, does not include ancillary emissions from leaching and surface runoff, as such information is not often available. As a result, our estimate is only driven by the direct N2O emissions from agricultural soils. This may represent a fundamental difference when comparing the results across different data sets. EDGAR and FAOSTAT incorporate both direct and indirect N2O emissions in estimating the global emissions. Additionally, the agricultural sources from which the emissions are tabulated for our model are different from other data sets. For example, EDGAR includes rice cultivation and crop residue in its estimate [28]. Another key difference between N2O_STAT and other models lies in the methodology of collecting the model inputs. The N2O_STAT model uses the measured N2O emissions reported from field experiments, whereas the other approaches derive their emissions by using intermediate data sets (e.g. fertilizer production, livestock counts) and apply emission factors to the corresponding data sets. The N2O_STAT model only considers physicochemical variables of the emissions, excluding the soil management practices that might contribute to the emissions. In addition, the methods used to measure N2O emissions in the field were different from one study to another; these differences are not taken into consideration in developing N2O_STAT.

The region-based analysis (USA, India, and China) indicates that our model gives lower estimates than other modelling efforts. The global N2O agricultural soil emission from N2O_STAT estimate is 9–20% lower than EDGAR and FAOSTAT. The major differences, as observed in Fig. 3c, are most prominent in India and China. In India, negative differences are depicted in Fig. 6c in the northern and central regions, while the positives are mainly to the west and south of the subcontinent. However, the finely resolved agricultural emissions of N2O in India [23], as well as from EDGAR and FAOSTAT, agree well with N2O_STAT (< 20% differences). It is to be noted that the estimate from Aneja et al. [23] was calculated for 2003. Despite this difference, there are similarities between these data sets with respect to the areas from which high emissions are estimated. Such similarities are not observed when we compared our model estimate with EDGAR.

Our approach is subject to uncertainty. In particular, our statistical analysis was restricted to parameters which were available in the measurement literature and in global databases. Thus, the analysis did not include parameters such as soil composition and porosity, which could also influence N2O emissions. We also do not take into account short-term changes in moisture and temperature which may result in enhanced N2O emissions. Further, data were not available to systematically incorporate differences in agricultural practices, such as the cultivation of more than one crop per year, or the use of multiple fertilizer applications in a year. This may account for some of the difference between our estimates and other estimates for China, where two crops are grown per year in many places.

Nevertheless, previous N2O emissions inventory approaches are also subject to large uncertainties. Our literature survey identified N2O emission factors from less than 0.1 to almost 10 kg N2O–N kg−1 N applied [29, 30]. This demonstrates the difficulty of using an emission factor approach to compute N2O emissions. In fact, diagnostic tests for our model indicated that N2O emissions are a nonlinear function of N input [22]. N2O_STAT can be used to estimate a median value for the N2O emission factor by calculating the ratio between N2O emission and applied N fertilizer in every grid cell of the map. We calculated the N2O emission factor for USA. In our calculation, we distinguished the two sources of N2O emissions, i.e. synthetic fertilizer and organic fertilizer, and determined emission factors for each of these sources. Our results suggest that for the USA, the median values for the emission factor for synthetic fertilizer and organic fertilizer are 1.03% and 1.52%, respectively, based on the N input from the fertilizer. The emission factor for synthetic fertilizer is comparable to those from Stehfest and Bouwman [12] (0.9%) and De Klein et al. [31] (1.0%).

5 Conclusion

N2O_STAT is a statistical model developed for characterizing atmospheric N2O emissions from agricultural soils. We obtained N2O emissions and physicochemical variables (i.e. air temperature, soil temperature, soil moisture, soil pH, and N input to the soil) from published journal articles since 2000. In comparison with other data sets, the model generates a lower global N2O estimate by 9–20% (N2O_STAT: 3.75 Tg N yr−1; EDGAR: 4.49 Tg N yr−1; FAO: 4.07 Tg N yr−1), but is ~ 25% higher when compared to Bouwman et al. [32] (2.80 Tg N yr−1). A region-based analysis (USA, India, and China) using the N2O_STAT model produces an estimate for the USA that ranges from − 13 to + 32% in comparison with other published data sets. Meanwhile, the N2O_STAT model estimate for India shows N2O emissions between − 56 and + 14% when compared to other data sets. A much lower estimate is seen for China, where the model estimates for N2O emissions are 38–177% lower than other data sets.

The N2O_STAT uses measured values for N2O emissions including N content in the fertilizer to develop the model. The correlations between N2O emissions and most physicochemical variables are at a high significance level (90%), suggesting that these variables are likely affecting the emissions despite excluding other variables. Moreover, the N2O_STAT model provides an opportunity to predict future N2O emissions in a changing world. This statistical model provides an innovative and relatively simple way to estimate global N2O emission from agricultural soils.

The underestimation of N2O emissions in comparison with other data sets and the fact that N2O_STAT may be still missing some key N inputs to its variables should be taken into account in future work. Parameterization of soil biological activity would more fully represent the processes governing the N2O emissions.



Support for this work was provided by U.S. GFDL-NOAA project NOAA CPO AC4. We thank Dr. Larry Horowitz and Dr. Fabien Paulot for their ongoing discussions on the project. We also thank Dr. Francesco Tubiello, UN Food and Agriculture Organization, for discussions of our results.

Author contributions

The five co-authors contributed equally to the work; however, VPA and WHS jointly supervised the work. AN prepared the global emission maps. All authors reviewed the manuscript. QL and AN performed the statistical analysis related to the modelling framework.

Compliance with ethical standards

Conflict of interest

The authors declare no competing interests.

Supplementary material

42452_2019_1688_MOESM1_ESM.docx (218 kb)
Supplementary material 1 (DOCX 217 kb)


  1. 1.
    Myhre G, Shindell D, Bréon F-M, Collins W, Fuglestvedt J, Huang J, Koch D, Lamarque J-F, Lee D, Mendoza B, Nakajima T, Robock A, Stephens G, Takemura T, Zhang H (2013) Anthropogenic and natural radiative forcing. In: Stocker TF, Qin D, G.-K.Plattner, Tignor M, Allen SK, Doschung J, Nauels A, Xia Y, Bex V, Midgley PM (eds) Climate change 2013: the physical science basis. Contribution of working group I to the fifth assessment report of the intergovernmental panel on climate change. Cambridge University Press, Cambridge, pp 659–740Google Scholar
  2. 2.
    Ravishankara AR, Daniel JS, Portmann RW (2009) Nitrous oxide (N2O): the dominant ozone-depleting substance emitted in the 21st century. Science 326:123–125. CrossRefGoogle Scholar
  3. 3.
    Forster P, Ramaswamy V, Artaxo P, Berntsen T, Betts R, Fahey DW, Haywood J, Lean J, Lowe DC, Myhre G (2007) Changes in atmospheric constituents and in radiative forcing. In: Solomon S, Qin D, Manning M, Chen Z, Marquis M, Averyt KB, Tignor M, Miller HL (eds) Climate change 2007. The physical science basis. Cambridge University Press, CambridgeGoogle Scholar
  4. 4.
    Flückiger J, Monnin E, Stauffer B, Schwander J, Stocker TF, Chappellaz J, Raynaud D, Barnola J-M (2002) High-resolution Holocene N2O ice core record and its relationship with CH4 and CO2. Global Biogeochem Cycles 16:1–8. CrossRefGoogle Scholar
  5. 5.
    Ciais P, Sabine C, Bala G, Bopp L, Brovkin V, Canadell J, Chhabra A, DeFries R, Galloway J, Heimann M (2014) Carbon and other biogeochemical cycles. In: Stocker TF, Qin D, Plattner G-K, Tignor M, Allen SK, Boschung J, Nauels A, Xia Y, Bex V, Midgley PM (eds) Climate change 2013: the physical science basis. Contribution of working group I to the fifth assessment report of the intergovernmental panel on climate change. Cambridge University Press, pp 465–570Google Scholar
  6. 6.
    Schlesinger WH, Bernhardt ES (2013) Biogeochemistry: an analysis of global change, 3rd edn. Academic Press, New YorkGoogle Scholar
  7. 7.
    IPCC (2006) Agriculture, forestry, and other land uses. In: Eggleston HS, Buendia L, Miwa K, Ngara T, Tanabe K (eds) 2006 IPCC guidelines for national greenhouse gas inventories. Volume 4: Agriculture. IGES, Hayama, Japan, pp 1.1–1.21Google Scholar
  8. 8.
    Smith P, Bustamante M, Ahammad H, Clark H, Dong H, Elsiddig EA, Haberl H, Harper R, House J, Jafari M, Masera O, Mbow C, Ravindranath NH, Rice CW, Abad CR, Romanovskaya A, Sperling F, Tubiello F (2014) Agriculture, Forestry, and Other Land Use (AFOLU). In: Edenhofer O, Pichs-Madruga R, Sokona Y, Farahani E, Kadner S, Seyboth K, Adler A, Baum I, Brunner S, Eickemeier P, Kriemann B, Savolainen J, Schlömer S, Stechow C von, Zwickel T, Minx JC (eds) Climate change 2014: mitigation of climate change. Contribution of working group III to the fifth assessment report of the intergovernmental panel on climate change. Cambridge University Press, CambridgeGoogle Scholar
  9. 9.
    Tubiello FN, Salvatore M, Rossi S, Ferrara AF, Fitton N, Smith P (2013) The FAOSTAT database of greenhouse gas emissions from agriculture. Environ Res Lett 8:15009. CrossRefGoogle Scholar
  10. 10.
    Butterbach-Bahl K, Baggs EM, Dannenmann M, Kiese R, Zechmeister-Boltenstern S (2013) Nitrous oxide emissions from soils: how well do we understand the processes and their controls? Philos Trans R Soc Lond B Biol Sci 368:20130122CrossRefGoogle Scholar
  11. 11.
    Granli T, Bockman OC (1994) Nitrous oxide from agriculture. Nor J Agric Sci Norw 12:1–128Google Scholar
  12. 12.
    Stehfest E, Bouwman L (2006) N2O and NO emission from agricultural fields and soils under natural vegetation: summarizing available measurement data and modeling of global annual emissions. Nutr Cycl Agroecosyst 74:207–228. CrossRefGoogle Scholar
  13. 13.
    Rezaei Rashti M, Wang W, Moody P, Chen C, Ghadiri H (2015) Fertiliser-induced nitrous oxide emissions from vegetable production in the world and the regulating factors: a review. Atmos Environ 112:225–233. CrossRefGoogle Scholar
  14. 14.
    Wang Y, Guo J, Vogt RD, Mulder J, Wang J, Zhang X (2017) Soil pH as the chief modifier for regional nitrous oxide emissions: new evidence and implications for global estimates and mitigation. Glob Change Biol 24:e617–e626. CrossRefGoogle Scholar
  15. 15.
    Oertel C, Matschullat J, Zurba K, Zimmermann F, Erasmi S (2016) Greenhouse gas emissions from soils: a review. Chem Erde 76:327–352. CrossRefGoogle Scholar
  16. 16.
    Yu T, Zhuang Q (2019) Quantifying global N2O emissions from natural ecosystem soils using trait-based biogeochemistry models. Biogeosciences 16:207–222. CrossRefGoogle Scholar
  17. 17.
    Janssens-Maenhout G, Crippa M, Guizzardi D, Muntean M, Schaaf E, Dentener F, Bergamaschi P, Pagliari V, Olivier JGJ, Peters JAHW, van Aardenne JA, Monni S, Doering U, Petrescu AMR (2017) EDGAR v432 global atlas of the three major greenhouse gas emissions for the period 1970–2012. Earth Syst Sci Data Discuss. CrossRefGoogle Scholar
  18. 18.
    EPA (2018) Inventory of U.S. greenhouse gas emissions and sinks: 1990–2016Google Scholar
  19. 19.
    Gronberg JM, Spahr NE (2012) County-level estimates of nitrogen and phosphorus from commercial fertilizer for the conterminous United States, 1987–2006. US Department of the Interior, US Geological Survey, Reston, VACrossRefGoogle Scholar
  20. 20.
    Gronberg JM, Arnold TL (2017) County-level estimates of nitrogen and phosphorus from animal manure for the conterminous United States, 2007 and 2012. Reston, VAGoogle Scholar
  21. 21.
    Kim D-G, Giltrap D, Hernandez-Ramirez G (2013) Background nitrous oxide emissions in agricultural and natural lands: a meta-analysis. Plant Soil 373:17–30. CrossRefGoogle Scholar
  22. 22.
    Shcherbak I, Millar N, Robertson GP (2014) Global metaanalysis of the nonlinear response of soil nitrous oxide (N2O) emissions to fertilizer nitrogen. Proc Natl Acad Sci 111:9199–9204CrossRefGoogle Scholar
  23. 23.
    Aneja VP, Schlesinger WH, Erisman JW, Behera SN, Sharma M, Battye W (2012) Reactive nitrogen emissions from crop and livestock farming in India. Atmos Environ 47:92–103. CrossRefGoogle Scholar
  24. 24.
    Garg A, Shukla PR, Kapshe M (2006) The sectoral trends of multigas emissions inventory of India. Atmos Environ 40:4608–4620. CrossRefGoogle Scholar
  25. 25.
    Sharma SK, Choudhury A, Sarkar P, Biswas S, Singh A, Dadhich PK, Singh AK, Majumdar S, Bhatia A, Mohini M, Kumar R, Jha CS, Murthy MSR, Ravindranath NH, Bhattacharya JK, Karthik M, Bhattacharya S, Chauhan R (2011) Greenhouse gas inventory estimates for India. Curr Sci 101:1–11. CrossRefGoogle Scholar
  26. 26.
    Gao B, Ju XT, Zhang Q, Christie P, Zhang FS (2011) New estimates of direct N 2O emissions from Chinese croplands from 1980 to 2007 using localized emission factors. Biogeosciences 8:3011–3024. CrossRefGoogle Scholar
  27. 27.
    Zhou F, Shang Z, Ciais P, Tao S, Piao S, Raymond P, He C, Li B, Wang R, Wang X, Peng S, Zeng Z, Chen H, Ying N, Hou X, Xu P (2014) A new high-resolution N2O emission inventory for China in 2008. Environ Sci Technol 48:8538–8547. CrossRefGoogle Scholar
  28. 28.
    IPCC (1996) Revised 1996 IPCC guideline for national greenhouse gas inventories, Common reporting framework: agricultureGoogle Scholar
  29. 29.
    Majumdar D, Kumar S, Pathak H, Jain MC, Kumar U (2000) Reducing nitrous oxide emission from an irrigated rice field of North India with nitrification inhibitors. Agric Ecosyst Environ 81:163–169. CrossRefGoogle Scholar
  30. 30.
    Shimizu M, Hatano R, Arita T, Kouda Y, Mori A, Matsuura S, Niimi M, Jin T, Desyatkin AR, Kawamura O, Hojito M, Miyata A (2013) The effect of fertilizer and manure application on CH4and N2O emissions from managed grasslands in Japan. Soil Sci Plant Nutr 59:69–86. CrossRefGoogle Scholar
  31. 31.
    De Klein C, Novoa RSA, Ogle S, Smith KA, Rochette P, Wirth TC, McConkey BG, Mosier A, Rypdal K (2006) N2O emissions from managed soils, and CO2 emissions from lime and urea application (Chapter 11). GenevaGoogle Scholar
  32. 32.
    Bouwman AF, Boumans LJM, Batjes NH (2002) Modeling global annual N2O and NO emissions from fertilized fields. Global Biogeochem Cycles 16:1–9. CrossRefGoogle Scholar
  33. 33.
    NOAA (2019) Halocarbon and other atmospheric trace gases: nitrous oxide (N2O)—dataset. Accessed 10 July 2019
  34. 34.
    Firestone MKK, Davidson EAA (1989) Microbiological basis of NO and N2O production and consumption in soil. Exch Trace Gases Between Terr Ecosyst Atmos 47:7–21. CrossRefGoogle Scholar

Copyright information

© Springer Nature Switzerland AG 2019

Authors and Affiliations

  1. 1.Department of Marine, Earth, and Atmospheric SciencesNorth Carolina State UniversityRaleighUSA
  2. 2.Cary Institute of Ecosystem StudiesMillbrookUSA

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