Optimization of Nitrogen Fertilizer Application with Climate-Smart Agriculture in the North China Plain

: Long − term excessive nitrogen fertilizer input has resulted in several environmental prob-lems, including an increase in N 2 O emissions and the aggravation of nitrate leaching; monitoring nitrogen fertilizer is crucial for maize with high yield. This study aimed to optimize the amount of nitrogen applied to maize by Climate − Smart Agriculture (CSA) so as to continuously improve agricultural productivity and reduce or eliminate N 2 O emissions as much as possible. Field experiments with a completely randomized design were conducted to examine the effects of six nitrogen treatments (N application levels of 0, 120, 180, 240, 300, 360 kg · ha − 1 , respectively) on N 2 O emissions, residual concentration of nitrate and ammonium nitrogen, maize yield, and nitrogen utilization efﬁciency in 2018 and 2019. The results indicated that the residual concentration of nitrate nitrogen (NO − 3 − N) in the two seasons signiﬁcantly increased; N 2 O emissions signiﬁcantly increased, and the nitrogen fertilizer agronomic efﬁciency and partial productivity of maize fell dramatically as the nitrogen application rate increased. The maize grain yield rose when the N application amount was raised (N application amount <300 kg · ha − 1 ) but decreased when the N application amount > 300 kg · ha − 1 . An increase in the nitrogen application rate can decrease nitrogen use efﬁciency, increase soil NO − 3 − N residual, and N 2 O emissions. Reasonable nitrogen application can increase maize yield and reduce N 2 O emissions and be conducive to improving nitrogen use efﬁciency. By considering summer maize yield, nitrogen use efﬁciency, and farmland ecological environment, kg N kg · ha − 1 could be utilized as the nitrogen threshold for summer maize in the North China Plain.


Introduction
Climate−Smart Agriculture (CSA) is an approach to developing agricultural strategies to secure sustainable food security during climate change. CSA includes three essential objectives: (1) improve the adaptability of agricultural production against climate change; (2) minimize agricultural greenhouse gas emissions as much as possible; (3) sustainably increase agricultural productivity and grower incomes. This is the main developing direction for global agricultural production to respond to climate change (www.fao.org, accessed on 9 July 2021). Reducing nitrogen fertilizer input and greenhouse gas emissions in agricultural production is of great significance to realizing CSA. Maize is one of the most widely planted and important food crops worldwide [1]. The application of nitrogen fertilizer is crucial for maize with high yield. However, long-term excessive nitrogen fertilizer input has brought a series of environmental safety problems, such as an increase in N 2 O emissions, the aggravation of nitrate leaching, and the promotion of soil and water acidification [2,3]. Although more yield can be obtained by increasing nitrogen application, the question is whether the increase in yield is sufficient to offset the negative

Experimental Design
The test site has been a long−term positioning test field for the winter wheat-summer maize rotation since 2012. A completely randomized design was used in this study. Moreover, six treatments were set up in the experiment: N0, N120, N180, N240, N300, N360 (nitrogen application rates were 0, 120, 180, 240, 300, 360 kg•ha −1 , respectively). Each treatment was 30 m long and 5 m wide with three replications. The maize variety was 'Denghai 605′, and it was planted in a north-south direction with 60 cm row spacing and 25 cm plant spacing. The planting date of summer maize in 2018 was June 10 and the harvest date was September 27; the planting date of summer maize in 2019 was June 14 and the harvest date was September 27. The amount of phosphate fertilizer and potassium fertilizer for the 6 treatments was the same when sowing: K2O−105 kg•ha −1 , P2O5−120 kg•ha −1 . Nitrogen fertilizer (urea) was applied twice; for the first application, nitrogen fertilizer was applied together with phosphorus and potassium fertilizer at sowing, and the second application in 2018 and 2019 were performed on July 13 and July 26, respectively. The ratio of base nitrogen fertilizer to top dressing was 50% to 50%.

Nitrous Oxide Sampling and Analysis
The nitrous oxide (N2O) released from the soil surface was tested by chamber gas chromatography, and the flux was then calculated. Regarding the size of the static chamber: length × width × height = 30 cm × 20 cm × 10 cm. The soil gas sampling was taken every 7 days. If there was any heavy rainfall, samples would be taken on the third day after the rainfall. This deferred treatment was intended to avoid the sharp rise in N2O emission flux caused by the increase in soil water filled porosity (WFPS) after rainfall. Due

Experimental Design
The test site has been a long−term positioning test field for the winter wheat-summer maize rotation since 2012. A completely randomized design was used in this study. Moreover, six treatments were set up in the experiment: N0, N120, N180, N240, N300, N360 (nitrogen application rates were 0, 120, 180, 240, 300, 360 kg·ha −1 , respectively). Each treatment was 30 m long and 5 m wide with three replications. The maize variety was 'Denghai 605', and it was planted in a north-south direction with 60 cm row spacing and 25 cm plant spacing. The planting date of summer maize in 2018 was June 10 and the harvest date was September 27; the planting date of summer maize in 2019 was June 14 and the harvest date was September 27. The amount of phosphate fertilizer and potassium fertilizer for the 6 treatments was the same when sowing: K 2 O−105 kg·ha −1 , P 2 O 5 −120 kg·ha −1 . Nitrogen fertilizer (urea) was applied twice; for the first application, nitrogen fertilizer was applied together with phosphorus and potassium fertilizer at sowing, and the second application in 2018 and 2019 were performed on July 13 and July 26, respectively. The ratio of base nitrogen fertilizer to top dressing was 50% to 50%.

Nitrous Oxide Sampling and Analysis
The nitrous oxide (N 2 O) released from the soil surface was tested by chamber gas chromatography, and the flux was then calculated. Regarding the size of the static chamber: length × width × height = 30 cm × 20 cm × 10 cm. The soil gas sampling was taken every 7 days. If there was any heavy rainfall, samples would be taken on the third day after the rainfall. This deferred treatment was intended to avoid the sharp rise in N 2 O emission flux caused by the increase in soil water filled porosity (WFPS) after rainfall. Due to the different distributions of rainfall in the maize growing season in 2018 and 2019, the sampling times of the two seasons were different (12 and 9 times in 2018 and 2019, respectively) so as to ensure that there was no extreme value in each sampling. Sampling was collected between 8 and 10 a.m. A 50 mL syringe was used to take 50 mL gas samples, respectively, at 0, 10, 20 min after the box was covered [16]. The collected samples were taken back to the laboratory afterwards and a gas chromatograph (Shimadzu, 2010 plus) was used for taking measurement.
The gas flux was calculated as described by Mehmood et al. [16]: where F denotes emission flux (mg m −2 h −1 ) and dc/dt denotes the rate of change in gas concentration; M represents the measured gas' mole mass (g mol −1 ); P represents atmospheric pressure (Pa); T represents the absolute temperature (K) inside the chamber; V and P 0 represent volume (mL) and pressure (Pa) at standard conditions, respectively; H denotes the height of the chamber above the level of the earth (cm). By adding up the daily flux of the sampled and non−sampled days, the annual cumulative emissions were calculated, then, the linear interpolation between the time intervals was used for estimation [17]: where TF is the total cumulative gas emission of the whole growing season (kg·ha −1 ); (F i+1 + F i ) is the sum of gas emissions from two adjacent observations (kg·ha −1 ), and (T i+1 − T i ) is the number of days between this sampling and the last sampling. The global warming potential of gases was calculated as follows: where GWP is global warming potential (kg·ha −1 ); TF−N 2 O is the total cumulative N 2 O emission (kg·ha −1 ). On the time scale of 100 years, the warming potential of N 2 O per unit mass is 298 times that of CO 2 [18].

Soil Sampling and Analysis
Before maize sowing, the representative sites were randomly selected in the field with different fertilizer treatments and soil samples of 0-40 cm layers were taken back to the laboratory to detect soil organic matter, alkali−hydrolyzed N, available K, and available P. Their detection methods were hydrated hot potassium dichromate oxidation−colorimetry, alkali hydrolysis diffusion method, Olsen method, and ammonium acetate extraction, respectively [19]. When collecting gas samples, 0~20 cm of soil was taken between rows placed in static boxes and repeated 3 times. The collected filtrate was used to measure the content of nitrate and ammonium nitrogen in soil by AA3−HR flow analyzer (SEAL Analytical). The mass water content of soil in 0~20 cm was determined by drying and weighing, which was used to calculate the WFPS [17]: where PD is the particle density of the soil, which was 2.65 g cm −3 ; VSWC is the measured soil volumetric water content (%); and BD is the soil bulk density, whose average value of the soil in 0~20 cm was 1.56 g cm −3 [20]. When collecting gas samples, the soil temperature of the entire range of 0-10 cm depth was measured by TESTO mini probe thermometer near the static box. Samples were taken from continuous three−meter lines in three adjacent rows and then harvested, dried, threshed, and weighed. Based on 60 cm row spacing and 25 cm plant spacing, the yield per unit area was converted into yield per hectare.
The following equations were used to calculate partial factor productivity of applied N (PFPN) and nitrogen agronomic efficiency (NAE) [21].

Statistical Analysis
The data consisted of N 2 O, NO − 3 −N, and ammonium nitrogen concentrations, maize yield, soil moisture content, and temperature, etc. Piecewise linear interpolation was used to estimate the threshold of nitrogen application. Piecewise linear interpolation needs to construct linear interpolation basis function on each interpolation node, and then make their linear combination. A one−way ANOVA and Duncan's Multiple New Range Test in SPSS 22.0 were performed to test the effects of different nitrogen application rates on all the data obtained in the experiment. Pearson's correlation analysis was used to determine the relationship between nitrogen fertilizer application and yield, NO − 3 −N residual, and N 2 O global warming potential.

Dynamics of Soil WFPS and Soil Temperature under Different Nitrogen Fertilizer Treatments
The soil water filled pore space and temperature in soil aeration zones can affect microbial activity, which is an important factor affecting N 2 O emission. The variation of soil WFPS in the two growing seasons was basically the same and both significantly increased under the influence of rainfall and irrigation ( Figure 2). One−way ANOVA revealed that there were differences in WFPS of 0~20 cm soil layer under different nitrogen treatments in 2018 (p < 0.05), and the WFPS of N0 and N120 were significantly lower than those of other treatments, but there was no significant difference in WFPS of 0~20 cm soil layer from N120 to N360. However, in 2019, there was no significant difference (p > 0.05) in WFPS of 0~20 cm soil layer among different nitrogen treatments ( Figure 2). The linear regression analysis between the two−year WFPS and the nitrogen application rate revealed that there was no linear relationship between nitrogen application rate and WFPS ( Table 2). The changing trend of soil temperature in the 0~10 cm layer within the two seasons was basically the same, showing a trend of initially increasing and then decreasing, which was similar to air temperature change (Figure 3). At the end of the growing period in 2018, the soil temperature in the 0~10 cm depth slightly increased, which was caused by the increase in air temperature and solar radiation intensity. The difference in soil temperature in the 0~10 cm layer between different nitrogen application rates was not significant (p < 0.05) and there was no linear relationship (Table 2) within the two years, which indicated that the factor affecting the change in temperature of 0~10 cm soil was not nitrogen fertilizer treatment but environmental temperature.

Effects of Different Nitrogen Treatments on Soil NO −
3 −N and Ammonium Nitrogen During the growth period, the NO − 3 −N content of each treatment increased with the increase in nitrogen fertilizer input ( Figure 4). However, the content of ammonium nitrogen in the soil of each treatment did not follow this pattern. In 2019, the contents of ammonium nitrogen and NO − 3 −N in each treatment decreased by 36.1% and 63.9%, respectively, compared with that of 2018. The soil ammonium nitrogen content of each treatment was not significantly affected (p > 0.05) by nitrogen fertilizer treatment in 2019, but there were differences in the soil ammonium nitrogen content of each treatment in 2018 ( Figure 4). The average NO − 3 −N content of N360 and N300 in 2018 and N360 in 2019 was significantly higher (p < 0.05) than that of other treatments (Figure 4). From Table 2, there was no significant linear correlation between nitrogen application rate and soil ammonium nitrogen, but a significant positive correlation with soil NO − 3 −N. However, the R 2 of the fitting equation was low, indicating that the relationship between nitrogen application rate and soil NO − 3 −N could have other functional relationships.  The ns stands for p > 0.05 and ** stands for p < 0.01; WFPS: soil water filled pore space.     The ns stands for p > 0.05 and ** stands for p < 0.01; WFPS: soil water filled pore space.  tively, compared with that of 2018. The soil ammonium nitrogen content of each treatment was not significantly affected (p > 0.05) by nitrogen fertilizer treatment in 2019, but there were differences in the soil ammonium nitrogen content of each treatment in 2018 ( Figure  4). The average NO -3 −N content of N360 and N300 in 2018 and N360 in 2019 was significantly higher (p < 0.05) than that of other treatments (Figure 4). From Table 2, there was no significant linear correlation between nitrogen application rate and soil ammonium nitrogen, but a significant positive correlation with soil NO -3 −N. However, the R 2 of the fitting equation was low, indicating that the relationship between nitrogen application rate and soil NO

Effects of Different Nitrogen Treatments on N2O Emission Flux, Cumulative Emission, and Global Warming Potential
The peak value of each treatment appeared after the input of nitrogen and water (irrigation, rainfall, topdressing) in the field ( Figure 5). The average N2O emission fluxes of the six treatments increased with the increase in nitrogen application rate for the two

Effects of Different Nitrogen Treatments on N 2 O Emission Flux, Cumulative Emission, and Global Warming Potential
The peak value of each treatment appeared after the input of nitrogen and water (irrigation, rainfall, topdressing) in the field ( Figure 5). The average N 2 O emission fluxes of the six treatments increased with the increase in nitrogen application rate for the two years, indicating a positive correlation between nitrogen application rate and soil N 2 O emission flux ( Table 2). The average N 2 O emission fluxes of N360 and N300 were significantly higher than those of the other four nitrogen treatments (p < 0.01). In addition, there was no significant difference in N 2 O cumulative emission flux and N 2 O global warming potential among N360, N300, and N240, and no significant difference was displayed among N120, N180, and N0. The GWP N 2 O of each treatment was > 0, which indicated that the summer maize field was the source of N 2 O emission. The warming potential of N 2 O with different nitrogen application rates was as follows: N0 < N120 < N180 < N240 < N300 < N360 (p < 0.001). In addition, there was a significant linear correlation between nitrogen application rate and the cumulative N 2 O emission and GWP (Table 2). was no significant difference in N2O cumulative emission flux and N2O global warming potential among N360, N300, and N240, and no significant difference was displayed among N120, N180, and N0. The GWP N2O of each treatment was > 0, which indicated that the summer maize field was the source of N2O emission. The warming potential of N2O with different nitrogen application rates was as follows: N0 < N120 < N180 < N240 < N300 < N360 (p < 0.001). In addition, there was a significant linear correlation between nitrogen application rate and the cumulative N2O emission and GWP (Table 2).

Yield, NAE, and PFPN of Applied N in Different Treatments
The grain yield of summer maize increased at first, and then decreased with the increase in nitrogen application rate; the highest yield treatment was N300 (Table 3). One−way ANOVA showed that there was no significant difference in yield among treatments except for N0 in 2018, and the difference among treatments in 2019 was not completely significant. The overall maize yield in 2019 was 30.14% lower than that in 2018, and NAE and PFPN decreased significantly with the increase in nitrogen application rate (p < 0.01). To some extent, increasing the application rate of nitrogen fertilizer will increase the yield of summer maize, but nitrogen use efficiency will decrease significantly.

Yield, NAE, and PFPN of Applied N in Different Treatments
The grain yield of summer maize increased at first, and then decreased with the increase in nitrogen application rate; the highest yield treatment was N300 (Table 3). One−way ANOVA showed that there was no significant difference in yield among treatments except for N0 in 2018, and the difference among treatments in 2019 was not completely significant. The overall maize yield in 2019 was 30.14% lower than that in 2018, and NAE and PFPN decreased significantly with the increase in nitrogen application rate (p < 0.01). To some extent, increasing the application rate of nitrogen fertilizer will increase the yield of summer maize, but nitrogen use efficiency will decrease significantly. NEA, nitrogen agronomic efficiency; PFPN, partial factor productivity of applied N. Different small letters mean the significant differences among various nitrogen treatments (p < 0.05). The same as below.

Threshold of Nitrogen Application Rate for Summer Maize
The N application rate was mathematically fitted with the grain yield, NO − 3 −N residual, and GWP N 2 O in 2018 and 2019 ( Figure 6) and the fitting curve was obtained (Table 4). According to the characteristics and piecewise linear interpolation method of each function, the extremum point or the inflection point was calculated. When the nitrogen application rate was 244.29 kg·ha −1 , the maximum grain yield was 10,383.17 kg·ha −1 . The inflection point of the function fitting equation between soil NO − 3 −N and nitrogen application rate appears at the nitrogen application rate of 180 kg·ha −1 . Furthermore, the piecewise lin-ear interpolation was used to study the threshold value of nitrogen application and an equation group was obtained: y = 0.0697x + 5.7892 (0~180 kg·ha −1 ), y = 0.1379x − 6.3739 (180~360 kg·ha −1 ). The results showed that when the N application rate was more than 178.34 kg·ha −1 , the soil NO − 3 −N content would sharply increase. Using the same method, the linear equation system of N 2 O warming potential response to nitrogen application rate can be obtained: y = 0.6005x + 227.5, y = 3.3624x − 236.42. The inflection point (x = 167.97 kg·ha −1 ) of N 2 O warming potential in the maize field was obtained by solving this equation system. In order to ensure that the maize yield would not be greatly reduced, 95% Yield max was taken as the lower limit of the N application threshold. According to the function, nitrogen application rate, residual nitrogen concentration, and GWP N 2 O were calculated. The function image is shown in Figure 6, and the calculation results are shown in Table 4. While considering the yield, soil, and greenhouse gas emissions, when the nitrogen application rate was 173.94~178.34 kg·ha −1 , the yield decreased by 4.39~5.00% compared with the maximum yield. Moreover, the residual concentration of NO

Effects of Nitrogen Application Rate on NO
-3 −N Residual in Soil In this study, before the long−term field experiment (2012), the soil NPK content was basically the same; after six years, NPK (nitrogen, phosphorus, and potassium) and soil organic matter (SOM) were different with the N fertilizer gradient test, and the temporal variability of NO -3 −N residual in each treatment was large ( Table 2). The rainfall in 2018 was 80% higher than that in 2019 (Figure 1). The precipitation of NO -3 −N and ammonium nitrogen caused by rainfall may be the reason why the average content of NO -3 −N in 0~20 cm soil in 2018 was 1.77 times higher than that in 2019. In 2018, the excess nitrate and ammonium nitrogen in N240, N300, and N360 soil could not be utilized by maize plants, resulting in a significant increase in residual NO -3 −N in soil, which was higher than before maize sowing in 2018. Weng et al. [22] reported that the accumulation of NO  The row labeled "Yield, NO − 3 −N residual, GWP N 2 O" means that these factors were used as y to fit the nitrogen application rate (x), respectively. The column labeled "Yield, NO − 3 −N residual, GWP N 2 O" means that the nitrogen threshold in the same line was brought into the y value obtained by the three fitting functions. ** F value means significant at the p = 0.001 levels, respectively (n = 36).

Effects of Nitrogen Application Rate on NO −
3 −N Residual in Soil In this study, before the long−term field experiment (2012), the soil NPK content was basically the same; after six years, NPK (nitrogen, phosphorus, and potassium) and soil organic matter (SOM) were different with the N fertilizer gradient test, and the temporal variability of NO − 3 −N residual in each treatment was large ( Table 2). The rainfall in 2018 was 80% higher than that in 2019 (Figure 1). The precipitation of NO − 3 −N and ammonium nitrogen caused by rainfall may be the reason why the average content of NO − 3 −N in 0~20 cm soil in 2018 was 1.77 times higher than that in 2019. In 2018, the excess nitrate and ammonium nitrogen in N240, N300, and N360 soil could not be utilized by maize plants, resulting in a significant increase in residual NO − 3 −N in soil, which was higher than before maize sowing in 2018. Weng et al. [22] reported that the accumulation of NO − 3 −N in 0~90 cm soil layer of N180, which had the highest summer maize yield in the NCP, was 49.4~314.3 kg·ha −1 , and the residual amount of NO − 3 −N in soil was also significantly different between different seasons. Fertilization, environmental climate factors, and plant uptake and utilization were the main factors affecting the residual concentration and temporal and spatial distribution of NO − 3 −N in dryland soil, this is similar to the seasonal difference of NO − 3 −N in 0~60 cm (Table 5). Yang et al. [23], through their study of the wheat-maize rotation system, found that the content of soil NO − 3 −N increased exponentially with the increase in the nitrogen application rate, within limits, indicating that nitrogen application in the maize season significantly affected soil NO − 3 −N residual. However, some studies also found that when nitrogen fertilizer application was lower than 240 kg·ha −1 , the content of NO − 3 −N in maize rhizosphere was not significantly affected [24]. Although the meteorological conditions in the growth period of maize in 2018 and 2019 were different, and the conditions of crop absorption and utilization were not completely the same, resulting in a large annual variation of NO − 3 −N residual, the law of NO − 3 −N residual increasing with the increase in the nitrogen application rate was still consistent with the existing research results. In this study, there was no significant difference in ammonium nitrogen content among different treatments during the maize growing season while there was a significant difference in NO − 3 −N content. As maize fields belong to dry farming fields, the nitrification process is dominant in the soil. Ammonium nitrogen, as the substrate of the nitrification process, will be consumed and transformed into NO − 3 −N [5] so that the content of ammonium nitrogen remains almost unchanged with the increase in nitrogen fertilizer (urea).

Effects of Nitrogen Application Level on N 2 O Emissions
Previous studies have shown that summer maize farmland soil is the primary source of N 2 O emissions [25,26]. In this study, the N 2 O emission fluxes, cumulative emissions, and global warming potential are all greater than zero, which also proves this conclusion. The effect of nitrogen application on N 2 O emissions from farmland was similar to previous studies that found that N 2 O emissions increase following the increase in nitrogen application level [27]. However, the changing trend of N 2 O emission flux was different between the two years. The reason for this could be that the content of soil NO − 3 −N in 2019 was significantly lower than that in 2018, and the changing trend was also different. With the augment of nitrogen application level, the emissions of N 2 O increased [27]. N 2 O emission flux can be affected by soil NO − 3 −N, ventilation, temperature, water content, and fertilizer application as well as weather changes such as rainfall, temperature, and other factors [28]. However, the impact of farmland on N 2 O emission fluxes is not a comprehensive effect caused by the simple superposition of various factors, but a comprehensive embodiment of the overall effect by the synthesis of multiple factors [22]. Therefore, the mechanism of the effect on N 2 O and emission flux from maize fields needs to be further studied. Urea is generally not advocated in high−efficiency, intensive, and sustainable agriculture; however, it is commonly used by local farmers. Considering the popularization of the test results, urea was selected as the nitrogen fertilizer in this study.

Confirmation of Nitrogen Application Threshold
It is complicated to confirm the threshold of nitrogen application for maize because the planting areas of maize are widely distributed around the world, with various regional conditions, numerous varieties, and the contrasting responses of maize to different nitrogen levels. Tong et al. [29] aimed to increase yield and reduce nitrogen loss and obtained a safe nitrogen application rate of 207.27 kg·ha −1 . Fang et al. [1] pointed out that the optimal nitrogen application rate for maize under the cover of biodegradable film and polyethylene film was 205 and 196 kg·ha −1 , respectively. Tonitto et al. [30] suggested that 200 kg N kg·ha −1 could be used as the recommended nitrogen application rate for the maize belt in the United States. Different regions, external conditions, and evaluation indexes will affect the determination of the optimal nitrogen application threshold. Based on the long−term location experiment of different nitrogen rates, the soil-crop-atmosphere was taken as the research object, and the soil NO − 3 −N residual, maize grain yield, and N 2 O warming potential were used as evaluation indexes. Therefore, the nitrogen application threshold was 173.94~178.34 kg·ha −1 , which could significantly reduce soil and air pollution while not significantly reducing maize yield. However, the results of this study also had some limitations. For example, there were great interannual differences in maize yield. The possible reasons for this include that the rainfall in the corn growing season in 2018 was 80% higher than in 2019 ( Figure 6) and the lower yield in 2019 was probably due to the "continuous cropping obstacle". At this time, taking yield as the index for estimating the N threshold may lead to a result deviation. Moreover, this study was a single point positioning test, therefore the results of this study cannot be directly applied to other areas with large differences in soil and climate factors. However, the purpose of this study was to improve the nitrogen threshold estimation and evaluation method according to CSA.

Conclusions
In the present study, the effects of nitrogen application rate on yield and environmental impacts of summer maize fields were evaluated by yield, N 2 O warming potential, and the average concentration of soil NO − 3 −N in growing season. The most obvious results from this research are as follows: with the increase in nitrogen application rate, the yield of summer maize initially increased and then decreased, soil NO − 3 −N content and N 2 O global warming potential increased exponentially. According to the characteristics of the function, the conclusion is drawn that the amount of nitrogen application at the maximum yield of summer maize was 244.29 kg·ha −1 , whereas the nitrogen application rate before the sharp increase in GWP−N 2 O was 167.97 kg·ha −1 . It was put forward that the amount of nitrogen application before the sharp rise in soil nitrate concentration was 178.34 kg·ha −1 . When the decrease was less than 5% compared to the maximum yield, the threshold of nitrogen application that could significantly reduce GWP−N 2 O and soil NO − 3 −N residual was 173.94~178.34 kg·ha −1 . The two−year test data are very limited, thus it is impossible to obtain the nitrogen fertilizer threshold that is very in line with local demand. Therefore, it is necessary to conduct long−term research in multiple places in the future, and it is best to enable the research to experience different rainfall years within the study region.