Browse Subject Areas

Click through the PLOS taxonomy to find articles in your field.

For more information about PLOS Subject Areas, click here.

  • Loading metrics

Is there a nitrogen fertilizer threshold emitting less N2O with the prerequisite of high wheat production?

  • Yuan Yi,

    Roles Writing – original draft

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Fujian Li,

    Roles Data curation

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Mingwei Zhang,

    Roles Formal analysis

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Yi Yuan,

    Roles Methodology

    Affiliation Zhenjiang Agro-Technical Extension Station No. 97, Zhenjiang City, Jiangsu Province, China

  • Min Zhu,

    Roles Writing – review & editing

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Wenshan Guo ,

    Roles Supervision (WG); (XZ)

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Xinkai Zhu ,

    Roles Investigation (WG); (XZ)

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

  • Chunyan Li

    Roles Funding acquisition

    Affiliation Laboratory of Crop Genetics and Physiology of Jiangsu Province / Co-Innovation Center for Modern Production Technology of Grain Crops / Wheat Research Institute, Yangzhou University, Yangzhou, China

Is there a nitrogen fertilizer threshold emitting less N2O with the prerequisite of high wheat production?

  • Yuan Yi, 
  • Fujian Li, 
  • Mingwei Zhang, 
  • Yi Yuan, 
  • Min Zhu, 
  • Wenshan Guo, 
  • Xinkai Zhu, 
  • Chunyan Li


Excessive use of synthetic nitrogen (N) fertilizer and lower nitrogen use efficiency (NUE) are threatening the wheat production in the middle and lower reaches of Yangtze River. Excess input of N fertilizers also results in severe environmental pollution, climate change and biodiversity loss. However, the study on reasonable nitrogen application and NUE improvement with the prerequisite of stable and high yield remains unexplored. In our study, the four different levels of nitrogen were applied to find out the nitrogen threshold which could be both friendly to environment and promise the stable and high yield. The experiment was carried out in Yangzhou University (Yangzhou, China). The wheat cultivar Yangmai 23 was selected as the research material. The four nitrogen levels were as follows: 0, 189, 229.5, and 270 kg ha-1. The results showed that the grain yield under the application of 229.5 kg ha-1 N was as high as that under 270 kg ha-1 N level, with the observation of 20.3% increase in agronomic efficiency. The N2O emission of 229.5 kg ha-1 N application was as low as that of 189 kg ha-1 N, but the grain yield and agronomic efficiency were significantly higher (11.9%) under 229.5 kg ha-1 treatment than the lower one. Taken together, this indicated the nitrogen level at 229.5 kg ha-1 could be identified as the fertilizer threshold, which will be beneficial for the future fieldwork.

1. Introduction

Wheat is a dominant crop used for human food and livestock feed in temperate countries [1]. China is the largest wheat producer in the world, with an annual sowing area of approximately 23.4 million ha and production of 105 million tons [2]. Due to the ubiquitous utilization of synthetic nitrogen (N) fertilizer, it is easier for China to feed 22% of the world’s population using only 9% of the available arable land [3]. The high input of synthetic N fertilizer has contributed to a substantial increase in wheat production in China [4]. Consequently, China has become the largest consumer of N fertilizer in the world, and over 30% of the world’s total consumption is used by China [5]. Based on field experiments and investigations, NARs have reached 270 kg ha-1 or more, which is much higher than suggested [6, 7]. However, the nitrogen use efficiency (NUE) of wheat cultivated in China is only between 24.8% and 35.7%, which is much lower than the typical level of 50% reported in most developed countries [8,9]. It is estimated that 1% increase in NUE could save about $1.1 billion annually [10]; hence, improving NUE is essential for the development of sustainable agriculture [11, 12].

Since the mechanisms underlying NUE are complicated [11], several nitrogen utilization parameters have been applied in previous papers to help grasp this complexity. Partial factor productivity (PFPN), the ratio of total grain output to applied N inputs, reflects the situation of incremental increase in yield that results from N application and the use efficiency of endogenous N resources absorbed by the plant [13]. Agronomic efficiency (AEN) is a method to estimate the efficiency of converting applied N to grain yield [12] and it is made up mainly of two physiological components, N apparent recovery efficiency (ARN) and N physiological efficiency (PEN) [12].

Due to the high N application rates (NAR) and the low NUE in China, a large portion of the N fertilizer is wasted and affects the environment around agricultural lands [14]. Apart from the contamination of ground and surface water, the N-related massive emission of greenhouse gas (GHG) and the consecutive contributions to global warming constitute a serious threat to crop production sustainability. It has been estimated that agriculture contributes approximately 84% and 52% of the global anthropogenic N2O and CH4 emissions, respectively [15], while it is only responsible for approximately 1% of CO2 emissions [16]. Due to the wide application of synthetic N since the pre-industrial era, the concentrations of CH4 and N2O in the atmosphere have increased by 148% and 18%, respectively [17]. Based on previous studies, the agricultural CH4 and N2O emissions are likely to increase by 60% over the next two decades because of these increasing N applications [18]. In China, the CH4 and N2O emissions from wheat fields were estimated to range from 7.4 to 8.0 kg CH4 year-1 and from 88.0 to 98.1 g N2O N year-1, respectively [19]. Zhang et al. estimated that approximately 7% of the GHG emissions from the entire Chinese economy are N-fertilizer-related emissions [20], while the contribution of synthetic fertilizer use to the total GHG emission from EU-15 countries is only approximately 2% [21]. Moreover, recent studies have shown that the potential greenhouse gas emissions associated with the agricultural N additions in the lower reaches of the Yangtze River are highest in China [22]; furthermore, anthropogenic soil acidification driven by N fertilization has significantly increased in rice-wheat double-cropping systems since the 1980s [23]. Hence, it is urgent to accommodate the needs of the expanding world population by developing highly productive agriculture; however, it is also necessary to simultaneously preserve the quality of the environment [24].

The middle and lower reaches of the Yangtze River, which have typical high-yield rice-wheat double-cropping systems, have important contributions to wheat production in China. However, the excessive use of synthetic nitrogen (N) fertilizer along with the lower nitrogen use efficiency (NUE) have become restraints for wheat production in this region. Using the appropriate NARs could help increase biomass production and decrease GHG emissions [25]. In field experiments, it has successfully been shown that significant reductions in the NAR and related environmental impacts are possible without significantly reducing the yield [26, 27]. A 20–25% reduction in the NAR in winter wheat, relative to present levels, is recommended in the southern part of China [28]. Accordingly, the important objectives of this study are as follows: (a) to determine whether it is possible to decrease the NAR from the conventional level used by local farmers (i.e., 270 kg N ha-1) by 15% or 30% without causing significant declines in yield while simultaneously reducing GHG emissions; (b) to measure the seasonal GHG emission as N2O and CH4; and (c) to investigate the correlation between the GHG emissions and nitrogen utilization parameters.

2. Materials and methods

A field experiment was conducted at the experimental station of Yangzhou University, China (32.39°N, 119.42°E). The site is located in the middle and lower reaches of the Yangtze River, which has a subtropical monsoon climate. The soil was a sandy-loam, and the soil properties (0–20 cm soil layer) were characterized using the methods previously described by Lu [29]. Before land preparation, composite soil samples (0–20 cm depth) were collected and analyzed using the methods described by Lu [29]. The soil contained 1.7% organic matter, 0.7 g kg-1 total N, 75.2 mg kg-1 available N, 54.8 mg kg-1 available P, and 181.2 mg kg-1 available K in the 2013/2014 growing season; additionally, the soil contained 1.3% organic matter, 0.6 g kg-1 total N, 67.2 mg kg-1 available N, 45.5 mg kg-1 available P, and 99.3 mg kg-1 available K in the 2014/2015 growing season. The main meteorological data from two wheat growing seasons were measured and are summarized in Table 1. The stages of wheat growing were classified and referred to previous study as follow [30]: sowing, over-wintering, jointing, stem elongation, booting, and maturing stages, which corresponded to 0, 41, 115, 129, 156 and 211 d after sowing, respectively, during the 2013/2014 growing season; and 0, 43, 120, 136, 162 and 213 d after sowing, respectively, during the 2014/2015 growing season.

2.1 Experimental design and field management

The field trial used a randomized complete block design with three replicates per treatment. Yangmai23, a locally adapted new cultivar with strong gluten, was planted and rotated with paddy rice in this experiment, and the cultivar was supplied by the Lixiahe Agricultural Research Institute of China. In the 2013/2014 growing season, the wheat was sown on October 28 and harvested on June 1. In the 2014/2015 growing season, the wheat was sown on November 2 and harvested on June 3. Each plot measured 7.5 m in length × 3 m in width and had a theoretical density of 225 seeds per m2. The four nitrogen levels were 0 (0N), 189 (LN), 229.5 (MN), and 270 (HN) kg N ha-1; moreover, the 30% and 15% reductions in the NAR (relative to the conventional NAR used by local farmers of 270 kg N ha-1) corresponded to 189 and 229.5 kg N ha-1, respectively. Fertilizers were applied as urea (nitrogen content of 46.3%). The fertilization was divided into four stages, including the before sowing, tillering, beginning of stem elongation and booting stages, which had 50%, 10%, 20% and 20% of the four designated fertilizer amounts, respectively. The four fertilization stages corresponded to 0, 38, 119, and 147 d after sowing, respectively, during the 2013/2014 growing season, and to 0, 39, 122, and 149 d after sowing, respectively, during the 2014/2015 growing season. For all treatments, 120 kg ha−1 P2O5 (calculated from super-phosphate) and 120 kg ha−1 K2O (calculated from potassium chloride) were applied before sowing to guarantee there was no stress related to the amount of phosphate and potassium [30].

2.2 Sampling and data collection

2.2.1 Grain yield and N content.

During the entire experiment, the dates of the key growth stages of crops were recorded. Wheat plants were harvested from 1m2 subplots to determine the number of effective spikes. The grain numbers per spike were counted from 50 selected spikes. Three samples were weighed to obtain the mean thousand-grain weight for each plot. All harvested samples were threshed, and the grain yield was standardized at 13% moisture content. The concentrations of N in grain and straw were determined by micro-Kjeldahl [31], followed by digestion in a H2SO4–H2O2 solution. The yield response was calculated as follows [32]: where YN is the grain yield (kg ha-1) at a certain level of applied N fertilizer, and Y0 is the grain yield (kg ha-1) without N application.

2.2.2 Nitrogen utilization parameters.

The calculations for the nitrogen utilization parameters were as follows [33, 34]: where UN is the total N uptake (kg ha-1) in the shoot, U0 is the total N uptake measured without N application, and FN is the rate of applied N fertilizer (kg ha-1).

2.2.3 CO2, CH4 and N2O fluxes.

After sowing, the dark static chamber/GC method was used to detect the CO2, CH4 and N2O fluxes between 9:00 am and 11:00 am every 7 days from November 9 to May 30 during the 2014–2015 season. At the same time, the soil temperature and soil moisture content were also measured (Fig 1 and S1 Table). The chamber covered a field area of 0.25 m2 and was placed on a fixed PVC frame located on each plot. The chamber was wrapped with a layer of sponge and aluminum foil to minimize the air temperature changes inside the chamber during the sampling period. The chamber was 0.5 or 1.1 m high and was adapted based on crop growth and plant height. Each sampling was subdivided five times in 10-min intervals. A fan was used to mix the gases in the chamber, which were then drawn off using a 20-ml gas-sampling syringe. The concentrations of CO2, CH4, and N2O were simultaneously detected using a gas chromatograph (Agilent 7890A, Shanghai, China) in the laboratory.

Fig 1. Soil temperature and soil moisture content during the 2014/2015 growing season.

The increase in the GHG concentration in the static chamber was calculated by linear regression. Fluxes were calculated based on the following formula [35].

Here, dc/dt is acquired from the linear regression equation. The value m is the molecular weight of trace gas, P indicates the atmospheric pressure (P = 1.013×105 Pa), R is the gas constant (R = 8.314 J/mol/K), and T is the air temperature in the chamber. V, H, and A are the volume, height, and area of the static chamber, respectively.

Sample sets were rejected unless linear regression yielded an r2 value greater than 0.90. The seasonal CH4, N2O and CO2 emissions were sequentially linearly determined based on the emissions between every two adjacent intervals in the measurements. The air temperature inside the chamber was monitored during gas collection, and it was calibrated for the flux calculation.

The emission factor (EF-N2O) refers to the percentage of N that is released in the form of N2O to the applied N nutrients. where EN and E0 are the cumulative NO2-N emissions (kg N ha-1) from the fertilized and unfertilized plots, respectively, and NAR represents the N application rate (kg N ha-1)

2.2.4. GWP and GHGI values.

The global warming potential (GWP) of a greenhouse gas depends on its life time. Considering a time horizon of 100 years, the N2O and CH4 warming potentials are estimated to be 298 and 25 times higher than the CO2 warming potential, respectively [36]. The net global warming potential (net GWP) excluded CO2 [36].

GHGI is related to grain yield, as described in Mosier et al. and Shang et al. [37, 38].

2.3 Statistical analysis

Data were subjected to statistical analysis (ANOVA) using the IBM SPSS 21.0 statistical package (SPSS, 2012). Emissions of CO2, CH4, and N2O followed a logarithmic distribution, and log transformations of these emissions were used for statistical analysis. Significant differences among means were determined by Duncan’s multiple range tests at P ≤ 0.05. Pearson’s bivariate correlation analysis was used to evaluate the relationships between GHG emission and both yield and nitrogen utilization parameters.

3. Results

3.1 Grain yield and protein content

As seen from Table 2, in two crop years, the grain yields increased significantly due to the application of more nitrogen fertilizer; however, yields reached a plateau at 229.5 kg N ha-1, after which the wheat yield was hardly affected by the NAR. Compared to the HN plot, the grain yield in the MN plot was almost the same (2014/2015 growing season) or even higher (2013/2014 growing season); however, the NAR could be efficiently reduced by 15%. In contrast, the wheat yields in the two growing seasons significantly decreased by 13.5% and 13.0%, respectively, when the NARs were reduced by 30% in the LN treatment, which negatively affected wheat production. Similarly, yield responses were almost the same between the MN and HN plots, and both were significantly higher than that of the LN plot. The responses of grains per spike to the NARs were positive; however, there were no significant differences in the number of effective spikes among the different nitrogen application treatments. The improvements in grain yield were mainly due to the interaction of grains per spike and thousand-grain weight. The protein content increased as more N was applied in the 2014/2015 growing season, but the protein content was even higher in the MN plot than in the HN plot during the 2013/2014 growing season.

Table 2. Effects of different nitrogen applications on grain yields of winter wheat.

3.2 Nitrogen utilization parameters

As shown in Table 3, in the two crop years, the AEN significantly increased by 20.3% and 16.2%, respectively, in the MN plot compared to the HN plot. Additionally, the AEN of the MN plot was higher than that in the LN plot in both years. The PFPN decreased significantly due to the increasing NAR, which reflected the law of diminishing returns. Thus, the 15% reduction in the NAR was an effective measure that improved the NUE without reducing the grain yield.

Table 3. Effects of different nitrogen application rates on nitrogen utilization parameters.

AEN can be further decomposed into the ARN and PEN of applied N. The ARN improved as the NAR increased, while the PEN was negatively affected by the increase in the NAR. In the 2013/2014 growing season, the ARN in the MN plot only had a slight reduction of 1.7%, which was not significant relative to the HN plot; however, the PEN in the MN plot was significantly higher than that in the HN plot.

3.3 Greenhouse gas (GHG) emissions, net GWP, and GHGI

3.3.1 GHG emissions.

As seen in Table 4, the CO2 released from soil and plants was the largest source of greenhouse gas emission in all treatments. It was observed that the cumulative CO2 emissions significantly increased with increases in the NAR during the 2014/2015 wheat growing season. There was no obvious relationship between the CH4 emissions and NAR, and the lowest cumulative emissions were measured in the MN plot. The cumulative N2O emissions gradually increased with increases in the NAR, and the values varied from 0.621 to 1.32 kg N ha-1, which were equivalent to 0.41%-0.48% of the N fertilizer that was applied. Relative to the HN plot, the seasonal N2O emissions significantly decreased by 19.1% in the MN plot. The MN practices emitted 16.6% more N2O because they received additional N through the higher application relative to the LN treatment; however, this difference was not significant. The emission factor (EF-N2O) relative to the applied N was measured to range from 0.144 to 0.258% in all nitrogen treatments. Compared to the HN plot, the EF-N2O decreased by 39.9% and 24.8% in the LN and MN plots, respectively.

Table 4. Total emission of greenhouse gas during whole growth period of winter wheat.

3.3. 2 Net GWP and GHGI.

The seasonal net GWP flux during 2014/2015 growing season was presented in Fig 2 and S2 Table. Higher net GWP fluxes occurred in the early of growing season, and the highest peak of net GWP fluxes were recorded at the 28 days after sowing. Peak net GWP flux increased with NAR, with rates ranging from 24.56 to 71.47 mg N m-2 h-1. The net GWP flux under all treatments were concentrated on the sowing-before wintering stage, accounting for 41.0–49.7% of total emissions from the whole wheat growth period. There were several small emission peaks in the next days. After stem elongation, the period of rapid wheat growth, fast uptake and utilization of soil N occurred, resulting in the slight peak of net GWP flux in the week after top-dressing under all N application conditions. At later stages, large amounts of soil N were absorbed and utilized for wheat growth along with rising temperature, leading to minor changes in net GWP under all N conditions.

Fig 2. Seasonal net GWP flux during 2014/2015 growing season.

0N: 0 kg N ha-1; LN: 189 kg N ha-1; MN: 229.5 kg N ha-1; HN: 270 kg N ha-1. Standard deviation (SD) is denoted by error bars. Arrows in the figure indicate the top-dressing time.

Although CH4 emissions were not obviously affected by N fertilization, N2O emissions significantly increased as N increased. Accordingly, the net GWP significantly increased with the increase in the NAR. Relative to the net GWP (631.8 kg CO2 eq ha−1 yr−1) from the HN plot, the net GWP was reduced by 61.1% and 62.1%, respectively, in the LN and MN plots. Compared to LN plot, the net GWP value was even lower than that in the MN plot.

The lowest GHGI was observed in the MN plot, which was 12.8% lower than the value in the 0N plot and 9.7% lower than the value in the HN plot. Hence, the MN practices provided ecological solutions for wheat production and, therefore, deserve considerable attention.

3.4 Correlation analysis between GHG emission and nitrogen utilization parameters

The results of correlation analysis between the nitrogen utilization parameters and the GHG emission index are shown in Table 5 and S3 Table. The N2O emission was negatively correlated with PFPN (r = - 0.999*, p < 0.05) and PEN (r = - 0.999*, p < 0.05), indicating that a reduction in N2O emissions improved the PFPN and PEN to some extent. Similarly, both CO2 and CH4 emissions were negatively correlated with the PFPN and PEN, and the trends were similar to those of the N2O emission. All these findings resulted in a negative correlation between the net GWP and the PFPN (r = - 0.940, p > 0.05) and PEN (r = - 0.904, p > 0.05). Furthermore, a negative correlation was also observed between the GHGI and the AEN (r = - 0.865, p > 0.05), PFPN (r = - 0.814, p > 0.05) and PEN (r = - 0.756, p > 0.05).

Table 5. Correlation analysis between GHG emissions and nitrogen utilization parameters.


4.1 Comparison of grain yield, AEN and N2O emission in wheat grown under 229.5 kg N ha-1 and 270 kg N ha-1

N application cannot promise a substantial increase in crop productivity due to the principle of diminishing returns [39]. Our grain yield under the application of 229.5 kg N ha-1 was as high as that under 270 kg ha-1 N level, which was accordant with previous studies [40, 41]. N application amount to winter wheat in Wuxi County has now been reduced by 20–45 kg N ha-1 or 10–20% without concomitant yield decreases, from formerly around 230 kg N ha-1 [42, 43]. Additionally, synthesized from an economic and ecological point of view, 150–225 kg N ha-1 is recommended in southern China [44]. Furthermore, significant increase (20.3%) of AEN was reported under 229.5 kg N ha-1 condition relative to 270 kg N ha-1 in our study, which were concordant with previous results that AEN gradually increased with N reducing [45, 46]. Thus, a quantum leap in the AEN is possible by simply reducing the N rate to 229.5 kg ha−1 in winter wheat; this reduction is primarily possible because the high N inputs of 270 kg N ha−1 in this region are excessive, and not all nitrogen is absorbed. The cumulative N2O emission gradually increased with N increasing in this paper, which was consistent with previous studies [47, 48]. Relative to 270 kg N ha−1, the seasonal N2O emissions was significantly decreased by 19.1% under 229.5 kg N ha-1 condition. Previously, a 10–30% reduction in N fertilizer would decrease N2O emissions by 11–22% in wheat [49], which were comparable with our findings. Meanwhile, N fertilizer reduction can lead to GHG emission reductions according to Kahrl's estimation [50]. Controlling the overall N rates to meet the needs of crop growth can help minimize N losses through N2O emissions. Hence, it is suggested that N2O emissions from wheat production can be reduced under the condition of 229.5 kg N ha-1 without yield reduction while AEN improved significantly. These findings demonstrated that the N loss could be greatly reduced due to the increased crop uptake.

4.2 Comparison of N2O emission, grain yield and AEN in wheat grown under 229.5 kg N ha-1 and 189 kg N ha-1

N2O is produced naturally in the soil through nitrification and denitrification and depends on soil mineral N contents [51]. The input of N fertilizers into agricultural systems is considered to be the dominant source of N2O emissions from agricultural soils [52, 53]. Since there exits significant correlations between N2O emissions and the amount of N applied [47, 48], N2O emissions gradually increased as more N input. However, in this study, no significant difference was observed on N2O emissions between 229.5 kg N ha-1 and 189 kg N ha-1. Hence, the practices of 229.5 kg N ha-1 provided ecological solutions for wheat production, therefore it deserved considerable attention. Grain yield was negatively affected with significant decrease under 189 kg N ha-1 condition compared to 229.5 kg N ha-1, which was consistent with previous studies [40, 41]. Based on the results of other studies, the AEN declines when rates exceed 150 kg N ha-1 [54]. However, the highest values were achieved when 229.5 kg N ha-1 was applied. Although our highest AEN (15.4 kg kg-1) was greater than the mean AEN for winter wheat in China (9.4 kg kg-1), as reported by Chuan et al. [32], it was still lower than the world average AEN for cereal crop production, i.e., 18 kg kg-1, as calculated by Ladha et al. [55]. It indicated that there still exists great potential for grain yield under the condition of 229.5 kg N ha-1. Generally, significant improvement in wheat production and AEN were achieved with fewer potential threats to environment and ecology under 229.5 kg N ha-1 condition.

4.3 Comparison of ARN and PEN in wheat grown under three nitrogen Levels

Reported by previous studies, ARN and PEN were negatively affected as increasing N input [11, 12], which reflected the principle of diminishing returns. It is well known that the PEN is very important to the AEN because improvements in the PEN directly result in greater plant biomass or grain yields. Normally, the stimulation effects of N fertilizer on PEN dramatically reduced due to excessive nitrogen fertilizer. An interesting finding showed that under 229.5 kg N ha-1 condition, the ARN was as high as it under 270 kg N ha-1, but the PEN was significantly higher, indicating that the N absorbed by the plant was utilized more efficiently under 229.5 kg N ha-1 condition. Though a slight reduction in PEN was found under 229.5 kg N ha-1 condition relative to 189 kg N ha-1 condition, the ARN was significantly increased, which explained that more N could be absorbed from soil under 229.5 kg N ha-1. All these findings illustrated that wheat plant could uptake and utilize more efficiently under 229.5 kg N ha-1, which was the reason why the highest AEN was achieved under 229.5 kg N ha-1.


Grain yields increased significantly due to higher nitrogen fertilizer input, but reach a plateau at 229.5 kg N ha-1, in which wheat yield is hardly affected by higher nitrogen input. Meanwhile, under 229.5 kg N ha-1 condition, the highest AEN value were achieved, and N2O emission was as low as that of 189 kg ha-1 N. These findings demonstrated the practice of 229.5 kg N ha-1 could be identified as a fertilizer threshold which was conductive to enhancing the sustainability of crop production in our research region. Whether it is also beneficial for other region or other cultivar is still remains unexplored.

Supporting information

S1 Table. Soil temperature and soil moisture content during the 2014/2015 growing season.


S2 Table. Seasonal net GWP flux during 2014/2015 growing season.


S3 Table. Effects of different nitrogen applications on grain yields, nitrogen utilization parameters and GHG emissions of winter wheat.



  1. 1. Shewry PR. Wheat. Journal of Experimental Botany. 2009; 60(6):1537–1553. pmid:19386614
  2. 2. Zheng J. Rice-wheat cropping system in China. Cal, 2000.
  3. 3. Cui Z, Chen X, Zhang F. Current nitrogen management status and measures to improve the intensive Wheat–Maize system in China. Ambio. 2010; 39(5–6):376–384. pmid:21053721
  4. 4. Peng S, Tang Q, Zou Y. Current status and challenges of rice production in China. Plant Production Science. 2009; 12(1):3–8.
  5. 5. Liu J, Diamond J. China's environment in a globalizing world. Nature. 2005; 435(7046):1179. pmid:15988514
  6. 6. Chen J, Huang Y, Tang Y. Quantifying economically and ecologically optimum nitrogen rates for rice production in south-eastern China. Agriculture, Ecosystems and Environment. 2011; 142(3):195–204.
  7. 7. Chen X, Cui Z, Peter MV, Kenneth GC, Pamela AM, Bai J, et al. Integrated soil-crop system management for food security. Proceedings of the National Academy of Sciences of the United States of America. 2011; 108(16):6399–404. pmid:21444818
  8. 8. Dobermann A, Cassman KG. Plant nutrient management for enhanced productivity in intensive grain production systems of the United States and Asia. Plant and Soil. 2002; 247(1):153–175.
  9. 9. Ma L, Feng S, Reidsma P, Qu F, Heerink N. Identifying entry points to improve fertilizer use efficiency in Taihu Basin, China. Land Use Policy. 2014; 37(2):52–59.
  10. 10. Kant S, Bi Y, Rothstein SJ. Understanding plant response to nitrogen limitation for the improvement of crop nitrogen use efficiency. Journal of experimental Botany. 2011; 62, 1499–1509. pmid:20926552
  11. 11. Sheoran P, Sardana V, Singh S, Kumar A, Mann A, Sharma P. Agronomic and physiological assessment of nitrogen use, uptake and acquisition in sunflower. International Journal of Plant Production. 2016; 10(2):109–122.
  12. 12. Xu G, Fan X, Miller AJ. Plant nitrogen assimilation and use efficiency. Annual review of plant biology. 2012; 63, 153–182. pmid:22224450
  13. 13. Nouriyani H, Majidi E, Seyyednejad SM, Siadat SA, Naderi A. Evaluation of nitrogen use efficiency of wheat (Triticum aestivum L.) as affected by nitrogen fertilizer and different levels of paclobutrazol. Research on Crops. 2012; 13(2):439–445.
  14. 14. Zhao X, Xie Y, Xiong Z, Yan X, Xing G, Zhu Z. Nitrogen fate and environmental consequence in paddy soil under rice-wheat rotation in the Taihu lake region, China. Plant Soil. 2009; 319(1–2):225–234.
  15. 15. Smith P, Martino D, Cai Z, et al. Greenhouse gas mitigation in agriculture. Philosophical Transactions: Biological Sciences. 2008; 363(1492):789–813.
  16. 16. Richard B, Dominic K, Kerstin S. Migration and Climate Change: Toward an Integrated Assessment of Sensitivity. Environment and Planning A. 2011; 43(2):431–450.
  17. 17. Chang I C. The physical science basis. Working group I contribution to the fourth assessment report of the IPCC. Computational Geometry. 2007; 18(2):95–123.
  18. 18. Li C, Salas W, De Angelo B, Rose S. Assessing alternatives for mitigating net greenhouse gas emissions and increasing yields from rice production in China over the next twenty years. Journal of Environmental Quality. 2006; 35(4):1554. pmid:16825476
  19. 19. Zou J, Huang Y, Qin Y, Liu S, Shen Q, Pan G, et al. Changes in fertilizer-induced direct N2O emissions from paddy fields during rice-growing season in China between 1950s and 1990s. Global Change Biology. 2009; 15(1):229–242.
  20. 20. Zhang J, Liu J, Zhang J, Cheng Y, Wang W. Nitrate-Nitrogen dynamics and nitrogen budgets in Rice-Wheat rotations in Taihu lake region, China. Pedosphere. 2013; 23(23):59–69.
  21. 21. European Environmental Agency. Annual European union greenhouse gas inventory 1990–2011 and inventory report 2013. European Environment Agency Copenhagen, 2013.
  22. 22. Tian H, Lu C, Melillo J, Ren W, Huang Y, Xu X, et al. Food benefit and climate warming potential of nitrogen fertilizer uses in China. Environmental Research Letters. 2012; 7(4): 044020.
  23. 23. Guo J, Liu X, Zhang Y, Shen J, Han W, Zhang W, et al. Significant acidification in major Chinese croplands. Science. 2010; 327(5968):1008–1010. pmid:20150447
  24. 24. Dyson T. World food trends and prospects to 2025. Proceedings of the National Academy of Sciences of the United States of America. 1999; 96(11):5929–5936. pmid:10339520
  25. 25. Snyder CS, Bruulsema TW, Jensen TL, Fixen PE. Review of greenhouse gas emissions from crop production systems and fertilizer management effects. Agriculture, Ecosystems & Environment. 2009; 133(3–4):247–266.
  26. 26. Meng Q, Sun Q, Chen X, Cui Z, Yue S, Zhang F. Alternative cropping systems for sustainable water and nitrogen use in the north China plain. Agriculture, Ecosystems and Environment. 2012; 146(1):93–102.
  27. 27. Jia X, Liu P, Zhao B, Gu L, Dong S, Bing S. Effect of different nitrogen and irrigation treatments on yield and nitrate leaching of summer maize (Zea mays L.) under lysimeter conditions. Agricultural Water Management. 2014; 137(1385):92–103.
  28. 28. Ju X, Liu X, Zhang F, Roelce M. Nitrogen fertilization, soil nitrate accumulation, and policy recommendations in several agricultural regions of China. Ambio. 2004; 33(6): 300–305. pmid:15387063
  29. 29. Lu R. Soil and agro-chemistry analytical methods. Vol. 15. 1999.
  30. 30. Zhu X, Guo W, Zhou J, Hu H, Zhang Y, Li C, et al. Effects of nitrogen on grain yield, Nutritional and Processing Quality of Wheat for Different End Uses. Agriculture Sciences in China. 2003; 2(6):609–616.
  31. 31. Chem A. Official methods of analysis of analytical chemistry, 1980.
  32. 32. Chuan L, He P, Pampolino MF, Johnston AM, Jin J, Xu X, et al. Establishing a scientific basis for fertilizer recommendations for wheat in China: Yield response and agronomic efficiency. Field Crops Research. 2013; 140(1):1–8.
  33. 33. Kumar A, Kumar A, Dwivedi A, Dhyani BP, Shahi UP, Sengar RS, et al. Production potential, nutrient uptake and factor productivity of scented rice in rice-wheat cropping system alongwith physicochemical and microbiological properties under site specific intergrated plant nutrient management. Journal of pure and applied microbiology. 2015; 8(2):1487–1497
  34. 34. Good AG, Shrawat AK, Muench DG. Can less yield more? Is reducing nutrient input into the environment compatible with maintaining crop production? Trends in Plant Science. 2004; 9(12):597–605. pmid:15564127
  35. 35. Guo Q, Li W, Liu D, Wu W, Liu Y, Wen X, et al. Seasonal characteristics of CO2 fluxes in a rain-fed wheat field ecosystem at the Loess Plateau. Spanish Journal of Agricultural Research. 2013; 11(4):980–988.
  36. 36. Gray V. Climate Change 2013—The physical science basis. South African Geographical Journal Being A Record of the Proceedings of the South African Geographical Society. 2010; 92(1):86–87.
  37. 37. Mosier AR, Ahlvorson AD, Reule CA, Liu X. Net global warming potential and greenhouse gas intensity in irrigated cropping systems in northeastern Colorado. Journal of Environmental Quality. 2006; 35(4):1584–1598. pmid:16825479
  38. 38. Shang Q, Yang X, Gao C, Wu P, Liu J, Xu Y, et al. Net annual global warming potential and greenhouse gas intensity in Chinese double rice-cropping systems: a 3-year field measurement in long-term fertilizer experiments. Global Change Biology. 2011; 17(6):2196–2210.
  39. 39. Cassman KG, Aobermann A, Walters DT, Yang H. Meeting cereal demand while protecting natural resources and improving environmental quality. Annual Review of Environment and Resources. 2003; 28(1):315–358.
  40. 40. Wang D, Liu Q, Lin J, Sun R. Optimum nitrogen use and reduced nitrogen loss for production of rice and wheat in the Yangtze Delta region. Environmental Geochemistry and Health. 2004; 26(2):221–227. pmid:15499777
  41. 41. Manna MC, Swarup A, Wanjari RH, Ravankar HN, Mishra B, Saha MN, et al. Long-term effect of fertilizer and manure application on soil organic carbon storage, soil quality and yield sustainability under sub-humid and semi-arid tropical India. Field Crops Research. 2005; 93, 264–280.
  42. 42. Roelcke M, Han Y, Cai Z, Richter J. Nitrogen mineralization in paddy soils of the Chinese Taihu region under aerobic conditions. Nutrient Cycling in Agroecosystems. 2002; 63(2–3):255–266.
  43. 43. Roelcke M, Yong H, Schleef KH, Zhu J, Liu G, Cai Z, et al. Recent trends and recommendations for nitrogen fertilization in intensive agriculture in eastern China. Pedosphere. 2004; 14(4):449–460.
  44. 44. Li C, Zhang Y, Cao M, Crill P, Dai Z, Froling S, et al. Comparing a process-based agro-ecosystem model to the IPCC methodology for developing a national inventory of N2O emissions from arable lands in China. Nutrient Cycling in Agroecosystems. 2001; 60(1–3):159–175.
  45. 45. Peng S, Buresh RJ, Huang J, Yang J, Zou Y, Zhong X. Strategies for overcoming low agronomic nitrogen use efficiency in irrigated rice systems in China. Field Crops Research. 2006; 96(1):37–47.
  46. 46. Raun WR, Solie JB, Johnson GV, Stone ML, Mullen RW, Freeman KW, et al. Improving nitrogen use efficiency in cereal grain production with optical sensing and variable rate application. Agronomy Journal. 2002; 94, 815–820
  47. 47. Eichner MJ. Nitrous oxide emissions from fertilized soils: summary of available data. Journal of Environmental Quality. 1990. 19:2(2):272–280.
  48. 48. Bouwman AF. Direct emission of nitrous oxide from agricultural soils. Nutrient Cycling in Agroecosystems. 1996; 46(1):53–70.
  49. 49. Johnson JM, Franzluebbers AJ, Weyers SL, Reicosy DC. Agricultural opportunities to mitigate greenhouse gas emissions. Environmental Pollution. 2007; 150(1):107–124. pmid:17706849
  50. 50. Kahrl F, Li Y, Su Y, Tennigkeit T, Wiles A, Xu J. Greenhouse gas emissions from nitrogen fertilizer use in China. Environmental Science & Policy. 2010; 13(8):688–694.
  51. 51. Yao Z, Zhou Z, Zheng X, Xie B, Mei B, Wang R, et al. Effects of organic matter incorporation on nitrous oxide emissions from rice-wheat rotation ecosystems in China. Plant Soil. 2010; 327:315–330.
  52. 52. Grant B, Smith WN, Desjardins R, Lemke R, Li C. Estimated N2O and CO2 emissions as influenced by agricultural practices in Canada. Climatic Change.2004; 65, 315–332.
  53. 53. Mosier A, Kroeze C, Nevison C, Oenema O, Seitzinger S, van Cleemput O. Closing the global N2O budget: nitrous oxide emissions through the agricultural nitrogen cycle. Nutrient Cycling in Agroecosystems. 1998; 52, 225–248.
  54. 54. Yan J, Shen Q, Yin B, Zhang S, Zhu Z, et al. Effects of fertilizer N application rate on yields and use efficiencies in Rice-Wheat rotation system in Taihu lake region. Soils. 2009.
  55. 55. Ladha JK, Patha H, Krupnik JS, Kessel C. Efficiency of fertilizer nitrogen in cereal production: retrospects and prospects. Advances in Agronomy. 2005; 87:85–156.