Apparent Accumulated Nitrogen Fertilizer Recovery in Long-Term Wheat–Maize Cropping Systems in China

Abstract

Recovery efficiency of nitrogen fertilizers has always been an important issue, especially for N fertilizer recommendation rate in cropping systems. Based on the equilibrium of N in the soil–plant system, apparent accumulated N fertilizer recovery (NRE_ac) was determined for long-term (15-years) experiments in wheat (Triticum aestivum L.) and maize (Zea mays L.) rotations at five field sites with various soils and climate characteristics in China. The result showed that the frequency of cropping and the content of soil clay affected NRE_ac positively and negatively, respectively. In the absence of nutrient deficiencies and other soil constraints (from NPK (nitrogen, phosphorus and potassium) in S2-CP (site2-Changping) in Beijing, S3-ZZ (site3-Zhengzhou) in Henan province and S4-YL (site4-Yangling) in Shaanxi province), NRE_ac had a narrow range from 70% to 78% with the highest average of 75% in wheat and maize cropping system. Meanwhile, the value 75% of NER_ac is a rational value proved by 3414 experiments. Additionally, the nitrate-N approach suggested that nitrate-N could be utilized by subsequent crops, the amount of which is calculated by the equation −1.23 × [(NO₃⁻-N) − 87]. Furthermore, another simpler and feasible method was proposed to maintain basic soil fertility while achieving a rational grain yield and maintaining a safe environmental upper threshold of nitrate. The present study provided a suit of methods for N fertilizer recommendations for the optimization of N applications in wheat and maize cropping system in China.

1. Introduction

The recovery efficiency of N fertilizers applied to crops (RE_N: the ratio of total N uptake by aboveground plant dry matter to the amount of fertilizer-N applied) has always been an important issue due to opposing goals [1]. On the one hand global food security must keep pace with an increasing world population, but at the same time there are legitimate concerns about environmental pollution caused by excess N applied to crops [1,2]. It is estimated that food demand will rapidly increase to 2.8 × 10⁹ t in 2030 and the corresponding consumption of fertilizer-N is predicted to be 9.6 × 10⁷ t compared with 7.8 × 10⁷ t year⁻¹ in 1995/1997 worldwide [3]. Especially in China, the total consumption of fertilizer-N has increased from 0.93 × 10⁷ t in 1980 to 2.39 × 10⁷ t in 2013 [4]. Fixen and West [5] reported that fertilizer-N supplies basic food needs for at least 40% of the global population and estimated that at least 60% of humanity will eventually owe its nutritional survival to fertilizer in the future. On the other hand, Chinese farmers always apply excess fertilizer-N to crops expecting to produce maximum yield. It is estimated that only 30–50% of applied N fertilizers are taken up by crops worldwide [6]. In China, Fixen and West [5] documented that AE_N (agronomic N use efficiency: kg grain per kg fertilizer-N) decreased from approximately 10–15 during 1958–1963 to 10 during 1981–1983 for wheat, and from 20–30 to 13.4 for maize. Consequently, environmental pollution due to excess N applied to crops is gradually becoming serious and a major cause for concern. Nitrate pollution in groundwater is one of the major pollution problems which have been reported in many countries such as the UK, Denmark, Belgium, France and India [7].

The need for food security and environmental protection is the paradox for fertilizer-N use [8,9]. Thus, a balancing between grain yield and the risk of nitrate-N loss is a common aim for both agronomists and environmentalists. Changes of RE_N, yield and soil NO₃⁻-N accumulation were subject to external factors, such as rate, place and time of applied N fertilizers, etc. As a result, Benbi and Biswas [10] reported that RE_N varied from 25 to 90% for both maize and wheat, which provided a possibility for mediating the paradox by improving fertilizer-N recommendation. The rate of N applied in the field was initially based on the theory of target yield fertilizer recommendation reported by Truog [11], and gradually improved with its widespread application [12,13,14,15,16,17], where determination of RE_N is the key. At present there are two methods, the difference and ¹⁵N isotopic methods, to estimate RE_N [18]. However, both methods have some assumptions. The former assumes that soil N uptake by the crop is the same for both fertilized and unfertilized N treatments, while the latter assumes that the isotope composition of the tracer is constant, soil microbial populations make no distinction between the ¹⁴N and ¹⁵N isotopes, and the chemical identities of isotopes are maintained in biochemical systems. In general, the value determined by the former is lower than the latter on soils with higher available N, and the former is higher than the latter on soils with lower available N, which the elusive soil nitrogen-supplying capacity could account for. Unfortunately, approaches to measure RE_N are not widely accepted across a wide range of soils [19,20,21].

Therefore, a feasible method to estimate RE_N is an agenda for fertilizer-N recommendation, especially in wheat–maize cropping system in China, which is a dominant cropping system with excessive N rate and high level of residual soil nitrate-N [22]. Accordingly, a long-term experiment of national soil fertility and fertilizers in wheat–maize cropping system was used in the present study. The objectives were to: (i) discuss the factors affected NRE_ac (NRE_ac: apparent accumulated N recovery efficiency); (ii) determine NRE_ac on the condition of nitrogen equilibrium in the soil–plant system [23,24]; (iii) further complete target yield N recommendation with regulating the relationship between N fertilization and utilization of soil NO₃⁻-N in the wheat–maize cropping system in China.

2. Materials and Methods

The data involved in this study was derived from a network of experiments in China, which was set up in 1990 to determine the response of crops to fertilizers on various types of soil under different climatic conditions. The study was composed of five sites, distributed in five districts: Urumqi (in Xinjiang province, icon S1-WQ), Changping (in Beijing, icon S2-CP), Zhengzhou (in Henan province, icon S3-ZZ), Yangling (in Shaanxi province, icon S4-YL) and Qiyang (in Hunan province, icon S5-QY), which dominate soils and climates of wheat and maize growing regions in China. Initial properties of soils are briefly listed in

Table 1. The experiment sites and initial properties.

	Sites
Items	S1-WQ	S2-CP	S3-ZZ	S4-YL	S5-QY
Location	Wulumuqi, Xinjiang	Changping, Beijing	Zhengzhou, Henan	Yangling, Shaanxi	Qiyang, Hunan
Longitude	87°25′58″ E	116°12′08″ E	113°39′25″ E	108°03′54″ E	111°52′32″ E
Latitude	43°58′23″ N	40°12′34″ N	34°47′02″ N	34°16′49″ N	26°45′12″ N
Mean annual temperature, °C	7.4	11.8	14.2	12.7	18.3
Annual rainfall, mm	247	577	644	542	1276
Cropping, per year	wheat or maize	wheat–maize	wheat–maize	wheat–maize	wheat–maize
Soil classification in China	Grey desert soil	Fluvo-aquic soil	Fluvo-aquic soil	Loessial soil	Red earth
Soil classification in FAO	Calcaric Cambisol	Haplic Luvisol	Calcaric Cambisol	Calcaric Regosol	Eutric Cambisol
Sand/Silt/Clay (%)	18.5/53.2/28.3	20.3/65.0/14.7	26.5/60.7/12.8	31.6/51.6/16.8	3.7/34.9/61.4
Soil pH (water/soil = 2.5)	8.1	8.2	8.3	8.6	5.7
Organic carbon (g kg−1)	8.8	7.1	6.7	6.3	6.7
Total N (g kg−1)	0.87	0.64	1.01	0.83	1.07
Total P (g kg−1)	0.67	0.69	0.65	0.61	0.45
Total K (g kg−1)	23	14.6	16.9	22.8	13.7

and more details can be found in Liu [25].

The present study included two cropping systems, one crop of wheat or maize per year in S1-WQ, another wheat–maize rotation per year at the other four sites. All experiments were unreplicated in a randomized design due to pressure on experiment land, where plot size varied between 100 and 468 m². Each experiment consisted of the following nine treatments: (1) CK (unfertilized), (2) PK (phosphorus and potassium), (3) N (nitrogen), (4) NK (nitrogen plus potassium), (5) NP (nitrogen plus phosphorus), (6) NPK (nitrogen, phosphorus plus potassium, (7) FS (NPK plus straw), (8) FM (NPK plus manure) and (9) HF (high NPK plus straw). Rates of fertilizers are shown in Liu et al. [25], in which the rates of manures or straw were based on N concentration, ratio of N from fertilizer to from manures or straws is 7:3, and the amounts of P and K were computed by P and K concentrations multiplied by the rates of applied manures or straw, respectively. Manures were applied after composting and straw was derived from corresponding treatments. All straw or manures were applied once-yearly as soon as the crop (wheat or maize) was harvested in S1-WQ, or wheat was harvested at the other four sites. The sources of N, P and K were urea, superphosphate and potassium chloride, respectively. Half of the N and all of the P and K were applied as basal fertilizer. The remainder of the N was applied as topdressing when needed. Irrigation was adjusted to annual precipitation when needed. When necessary, weeding by hand and pesticide applications were implemented.

2.1. Sampling and Analysis

Crops were harvested manually close to the ground with sickles at maturity and totally removed from the plots. Grain and straw were laid out in the sun on concrete slabs before threshing and then oven-dried at 65 °C to uniform moisture level before weighed, and then ground to pass a 0.15-cm sieve and stored for analysis. Plant samples to be tested were from the center of the plot in order to minimize marginal effects.

Soil samples were collected from the plough layer (0–20 cm) at the start of the experiment and between crop harvest and fertilizer application each autumn. At least five cores in each plot of each site were taken with a 5-cm diameter auger. Cores from the same plot were mixed thoroughly and air-dried, ground to pass through a 2.0-mm sieve and stored for analysis.

Plant samples were analyzed for total nitrogen using the micro-Kjeldahl digestion method, while soil samples were analyzed for total nitrogen, total phosphorus and total potassium using micro-Kjeldahl digestion, colorimetric analysis and a dissolution-flame photometer, respectively [26].

2.2. Calculation and Statistical Analysis

Based on mass balance theory, apparent accumulated N recovery efficiency (NRE_ac%) was calculated as total N uptake (N_p, in kg ha⁻¹) by crops (grain and straw) divided by total N rate (N_f, in kg ha⁻¹) using the following equation:

$${\mathrm{NRE}}_{\mathrm{ac}}\%=\frac{{{\displaystyle \sum }}_{\mathrm{i}=1}^{\mathrm{i}=\mathrm{n}}{\mathrm{N}}_{\mathrm{pi}}}{{{\displaystyle \sum }}_{\mathrm{i}=1}^{\mathrm{i}=\mathrm{n}}{\mathrm{N}}_{\mathrm{fi}}}\times 100$$

(1)

where i is the number of cultivation years and the maximum value of n is 15 years in the present study. Np has been calculated in the companion paper [25] using the following equation:

$${\mathrm{N}}_{\mathrm{P}}{=\mathrm{Yield}}_{\mathrm{wheat}}\times 2{.73\%+\mathrm{Yield}}_{\mathrm{maize}}\times 2.21\%$$

(2)

where Yield_wheat and Yield_maize represent the grain yields of wheat and maize (kg ha⁻¹), respectively, and 2.73% and 2.21% were the corresponding N concentrations in the aboveground biomass of wheat and maize, respectively. Moreover, on the principle of yield-based N recommendations [12,27], the following equation was used to compute a recommended N rate:

$${\mathrm{N}}_{\mathrm{f}.\mathrm{opt}}=\frac{{\mathrm{N}}_{\mathrm{p}}}{{\mathrm{NRE}}_{\mathrm{ac}.\mathrm{opt}}\%}$$

(3)

where NRE_ac.opt is an optimal NRE_ac with application of an economically optimal N rate (N_f.opt). In the present study, NRE_ac.opt is the average of NRE_ac from NPK treatment in S2-CP, S3-YL and S4-ZZ, and the value is 75%.

In order to assess the reliability of N rate recommended by Equation (3), the experiment with ‘3414w design was introduced into the present study, which is one of D-optimal design for quadratic regression [28]. In the experiment of ‘3414′ design, 3 represents 3 factors (nitrogen, phosphorus and potassium), 4 represents 4 rates of factors (0, 50% normal rate, normal rate and 150% normal rate), and 14 represents 14 treatments. Since 2005, the “3414” experiment was carried out nationwide that is a standard method for fertilizer recommendation in China [29]. Four of the 14 treatments were selected in the present study and they were N0P2K2, N1P2K2, N2P2K2 and N3P2K2, where N0, N1, N2 and N3 represent nitrogen rates and P2 and K2 represent appropriate phosphorus and potassium rates in the locality, respectively. More details are shown in Appendix A and Appendix References. A quadratic curve fitted the data was as follows:

$${\mathrm{Yield}=\mathrm{a}\times \mathrm{N}}_{\mathrm{f}}{}^2{+\mathrm{b}\times \mathrm{N}}_{\mathrm{f}}{+\mathrm{Yield}}_0$$

(4)

where Yield is grain yield (kg ha⁻¹), N_f is the rate of applied N, Yield₀ is an intercept, defined as a basic grain yield (kg ha⁻¹) without applied N, a and b are two coefficients.

N_f.opt is reached when

$$\frac{\partial \mathrm{Yield}}{\partial {\mathrm{N}}_{\mathrm{f}}}{=2\mathrm{aN}}_{\mathrm{f}.\mathrm{opt}}+\mathrm{b}=\mathrm{P}$$

(5)

where P equals the ratio of the cost of 1 kg fertilizer N to the price of 1 kg grain yield, and there are 2.33 (±0.28) and 2.76 (±0.50) for wheat and maize, respectively in the present study [30] and the variance of P does not make sense to the results of the study. Therefore, N_f.opt was calculated by the following equation:

$${\mathrm{wheat}:\mathrm{N}}_{\mathrm{f}.\mathrm{opt}}=\frac{2.33-\mathrm{b}}{2\mathrm{a}}{;\mathrm{maize}:\mathrm{N}}_{\mathrm{f}.\mathrm{opt}}=\frac{2.76-\mathrm{b}}{2\mathrm{a}}$$

(6)

Based on the ‘3414′ design and Equations (4) and (6), the following equation fitted the relationship between Yield_opt and Yield₀:

$${\mathrm{Yield}}_{\mathrm{opt}}{=\mathsf{\alpha }\times \mathrm{Yield}}_0$$

(7)

where Yield_opt is a grain yield at N_f.opt and α is a coefficient.

Statistical analyses were performed using SPSS analytical software (SPSS Inc., Chicago, IL, USA; version 19). Linear regression was used to determine the relationship between N_f.opt with estimatied by NRE_ac and measured in “3414” experiments, and correlation between yield_opt and yield₀. A quadratic curve regression was used to fit the response of yield to N application in “3414” experiments. Analysis of variance (ANOVA) was used to test the differences of NRE_ac% among treatments and experiment sites.

3. Results

3.1. Factors Affecting NRE_ac

Apparent accumulated nitrogen recovery efficiencies (NRE_ac) for the whole years of cultivation (15 years) are shown in

Table 2. Table2. Average of NRE_ac during 15 years at all sites.

Treatment	Experiment Site (%)
	S1-WQ1	S1-WQ2	S2-CP	S3-ZZ	S4-YL	S5-QY
N	149 ab	40 b	39 e	43 f	40 c	24 e
NK	115 bc	38 bc	47 d	50 e	42 c	30 d
NP	155 ab	58 a	66 b	77 a	70 b	39 c
NPK	161 a	62 a	70 a	78 a	77 a	43 b
FS	103 c	51 ab	48 d	64 c	74 ab	47 ab
FM	50 d	43 b	65 b	70 b	78 a	49 a
HF	31 d	26 c	58 c	56 d	71 b	47 ab

Note: different letters indicate significance at 0.05 levels in a column; S1-WQ1 was an experiment at S1-WQ from 1990 to 1994 and S1-WQ2 from 1995 to 2004.

. Values of NRE_ac for all treatments have a wide variation that ranged from 24 to 161%. Except all treatments in S5-QY and S1-WQ1 during 1991–1994, and N in S2-CP and S4-YL, NRE_ac from the same treatment were always higher in the wheat–maize rotation per year (in S2-CP, S3-ZZ and S4-YL) than in the wheat–maize-maize rotation per 3 years (in S1-WQ2). And averages of the former were 40, 46, 71, 75, 62, 71 and 62 for N, NK, NP, NPK, FS, FM and HF treatments, respectively. When comparing NRE_ac among treatments combined application of N, P and K in all experimental sites, there were also discrepancies. NRE_ac from the NPK treatment were always higher than that from incomplete nutrients treatments, in which the values from NP were the highest followed by that from NK and N in all experiment sites (except from N and NK in S1-WQ2). Especially, NRE_ac from NPK was significant higher in S1-WQ1 with lower N input than in S1-WQ2 with normal N input. There were no significant differences among NRE_ac from NPK in the wheat–maize rotation per year (in S2-CP, S3-ZZ and S4-YL) and the average of NRE_ac was 75% with a standard deviation of 6% (Figure 1).

On the other hand, NRE_ac was also affected by N rates. The higher N rates (HF) are always lower than normal N rates in NRE_ac in all sites except S5-QY. Due to its location in the subtropical humid climate zone characterized by higher temperature (mean annual temperature 18.3 °C) and intensive precipitation (the sum of precipitation from Mar. to Aug. accounting for 70% of precipitation in a whole year), values of NRE_ac from inorganic N treatments (N, NK, NP and NPK) are the lower than the combined treatments of inorganic and organic N in S5-QY. These results were mainly attributed to decreasing soil pH. At the start of experiment, the initial soil pH in S5-QY was 5.7, where the growth of wheat and maize might be restricted. Furthermore, N fertilization accelerated soil acidification. In 2005, soil pH decreased approximately to 4.

3.2. Assessment of N_f.opt and Relationship between Yield_opt and Yield₀

Using 3414 data, correlations between N_f·opt estimated by NRE_ac and N_f·opt measured with a quadratic curve are illustrated in Figure 2. For both of wheat and maize, the values of r² are above 0.9 with significant relationships (p < 0.01) which suggested that NRE_ac of 75% from NPK in S2-CP, S3-ZZ and S4-YL is an optimal NRE_ac. Meanwhile, relationships between Yield_opt and Yield₀ were illustrated in Figure 3, where values of r² are 0.62 and 0.73 for wheat and maize, respectively. And both correlations are significant (p < 0.01).

4. Discussion

NRE_ac are affected by cropping, soil properties and the environment, etc. Usually, crop rotation has higher nutrients recovery efficiency than monoculture. Long-term studies showed that crop rotation contributed to maintaining higher production levels [31]. Furthermore, the present study proved that the frequency of crop rotation could strengthen the trend outlined by Peterson and Varvel [32,33,34]. Without nutrient deficiency (from NPK, FS, FM and HF), NRE_ac in a three-year rotation (S1-WQ2) was always far lower than from a one-year rotation except in S5-QY (Table 2 and Figure 1). Moreover, soil texture might have an effect on mineralization and immobilization of soil nitrogen that finally influenced NRE_ac. In the present study, clay content in S1-WQ and S5-QY were higher than in the other three sites (Table 1). Consequently, all NRE_ac from sufficient nutrients were lower in S1-WQ2 and S5-QY than that in the other sites (Table 2 and Figure 1). This result was consisted with Hassink [35], who found that there was a significant negative relationship between clay content and the N mineralization rate. Soil pH is another soil property that affected NRE_ac. There was an initial lower soil pH of 5.7 (Table 1) and gradual acidification due to continuous N fertilization in S5-QY. Liu et al. [25] discussed the determinant for plant growth due to decreasing pH, and eventually a lower NRE_ac irreversibly occurred. In general, providing enough nutrients without other soil limitations in the same cropping period (S2-CP, S3-ZZ and S4-YL), NER_ac from NPK had a narrow variation with a range of 6 and maintained a higher level (average of 75%) (Table 2 and Figure 1).

The response of grain yield to applied N from NPK treatments is classically illustrated in Olfs et al. [8]. Grain yield increased with gradually increasing rate of applied N, which followed by an inflection point called an economically optimal yield (Yield_opt) when the profit from an increased yield of added N equalled zero. The corresponding applied N rate is called the economically optimal N rate (N_f.opt). Especially in the present study, grain yields were not significantly different between NPK and high N fertilization (HF) [25]. Therefore, based on the responses of grain yield to applied N [8], it was inferred that grain yield from NPK could be the Yield_opt and the corresponding N rate was equal to N_f.opt. Furthermore, there is a good correlation of N_f.opt between estimated by NRE_ac (75%) and measured using a quadratic curve-fitting with data from the ‘3414′ design (Figure 2), which reconfirmed that the inference is correct. Therefore, the present study concluded that NRE_ac of 75% could be equivalent to NRE_ac._opt and Equation (3) could be used to estimate N_f.opt in wheat–maize cropping systems in China.

When the N rate exceeds crop N requirement, there is an accumulation of NO₃⁻-N in the soil profile [36,37] as shown in Olfs et al. [8]. Moreover, the accumulated trend could be strengthened gradually with a further increasing N rate [8,38]. Previous research found that the content of NO₃⁻-N from the NPK treatment used in the present study were lower in the 0–90 cm soil profile (approximate 100, 30 and 60 kg ha⁻¹ in S2-CP, S3-ZZ and S4-YL, respectively) [39,40,41] which did not exceed the critical value of soil nitrate-N (a range of 66–118 kg ha⁻¹) in the top 90 cm of the soil profile for high yield in the wheat–maize cropping system [22,42]. Moreover, nitrate accumulation did not occur in the deeper soil profile [39,40,41]. All of these observations suggested that N rates from the NKP treatment would be the rational N rates again and further confirmed that the N rates could maintain the apparent N balance of a soil–plant system in the three sites.

However, accumulation of NO₃⁻-N in soil profile and nitrate leaching into ground water were serious and prevalent in wheat–maize cropping system in China [43]. Initially, agronomist have focused on NO₃⁻-N accumulation mostly for environment pollution [44] and gradually utilized them by the subsequent crop [22,42,45]. Cui et al. [42] reported that NO₃⁻-N content in the top 90 cm soil should be maintained at a level of about 87 kg ha⁻¹ after maize harvest. Furthermore, the numerical relationship between residual soil-N and applied N was that 1 kg soil NO₃⁻-N in the 0–90 cm soil profile was equivalent to 1.23 kg fertilizer-N [42]. The right side in Equation (3), therefore, should add N_s to utilize the abundant NO₃⁻-N using the following equation:

$${\mathrm{N}}_{\mathrm{s}}=-1.23\times \left[\left({\mathrm{NO}}_3{}^{-}-\mathrm{N}\right)-87\right]$$

(8)

where NO₃⁻-N means the nitrate-N content (kg ha⁻¹) in the top 90 cm soil profile, where 87 kg ha⁻¹ is a critical value of soil NO₃⁻-N balancing the benefits between the economy and the environment. In other words, neither the nitrate leaching risk nor depletion of NO₃⁻-N happens in a soil profile while the content of soil NO₃⁻-N is maintained at the critical value.

The nitrate-N approach, however, would already provide a method to utilize the abundant soil residual N, but implementation of the method is a challenge. One of the reasons is that the interval between the growth of maize and wheat is too short to determine soil nitrate in the wheat–maize cropping system in China. Additionally, the extension of the soil test at the farm level would be insurmountable due to the number of small farms involved. Therefore, a more feasible way for using N_s was needed in the present study. Fortunately, Cui [22,42] reported that the relationship between grain yield of wheat and maize and initial soil NO₃⁻-N content in the top 90 cm of the soil profile before sowing were fitted by the following equations:

$${\mathrm{RY}}_{\mathrm{wheat}}(\%)={0.16\times \mathrm{NO}}_3{}^{-}-\mathrm{N}+67.8$$

(9)

$${\mathrm{RY}}_{\mathrm{maize}}(\%)={0.21\times \mathrm{NO}}_3{}^{-}-\mathrm{N}+60.4$$

(10)

where RY_Wheat and RY_Maize are the relative yields to the local highest yields of wheat and maize, respectively. And 0.16 and 0.21 were numerical relationships between relative grain yield and initial NO₃⁻-N (0–90 cm soil profile) for wheat and maize, respectively.

To maintain yields at a rational level, the content of soil NO₃⁻-N has to keep up with the critical value. Combining of Equations (8)–(10) and Figure 3, N_s could be calculated, called a basic soil productivity approach, using the following equations:

$${\mathrm{N}}_{\mathrm{s}}=-1.23\times \left(\frac{\left({(\mathrm{Yield}}_{\mathrm{opt}}-2615)/\left({0.923\times \mathrm{Yield}}_{\mathrm{opt}}\right)\right)\times 100-81.7}{0.16}\right)$$

(11)

$${\mathrm{N}}_{\mathrm{s}}=-1.23\times \left(\frac{\left({(\mathrm{Yield}}_{\mathrm{opt}}-2282)/\left({1.102\times \mathrm{Yield}}_{\mathrm{opt}}\right)\right)\times 100-78.7}{0.21}\right)$$

(12)

where 81.7(%) and 78.7(%) are two critical values of RY_wheat and RY_maize, respectively. Exceeding the values means that N rate should be reduced in order to crop unitizing N from the abundant soil NO₃⁻-N. Yield_opt is a goal yield that was estimated by an average of recently five-year yields multiplied by 1.1 [46]. Therefore, the abundant soil NO₃⁻-N could be utilized by a basic soil productivity approach more easily than a nitrate-N approach.

In general, yield-based N fertilizer recommendations were not completely accepted by agronomists and farmers at its inception due to limitations such as yield variability [47,48], uncertainty of N recovery efficiency estimated by the difference or isotopic methods [18] because of the complexity of the soil-supplying N capacity [19,20,21]. However, based on the present study, the theory of yield-based N fertilizer recommendation was further improved. Particularly, it could be adapted in the wheat–maize cropping areas in China.

5. Conclusions

Apparent accumulated nitrogen recovery (NRE_ac) was affected by a multitude of factors. The present result that the three-year rotation (S1-WQ2) was always far lower than from the one-year rotation in NRE_ac suggested that a frequent of crop rotation affected the N cycle. Moreover, soil texture also affected NRE_ac. In S1-WQ and S5-QY with higher soil clay contents, NRE_ac from all treatments were always lower than that in the other sites with lower soil clay contents. In general, from the NPK treatment in S2-CP, S3-ZZ and S4-YL, the nitrate contents were lower and its accumulation did not occur in the soil profile. In other words, the present study provided evidence that N applied from the NPK treatment maintained an apparent N balance in the soil–plant system in the three sites. Meanwhile, NER_ac had a narrow variation with a range of 6% and maintained a higher level (average of 75%). Furthermore, grain yield from NPK in the three sites were the Yield_opt where NRE_ac could be equal to that at N_f.opt. Additionally, based on the fact of accumulation of NO₃⁻-N in the soil profile being serious and prevalent in the wheat–maize cropping system in China, NO₃⁻-N should be utilized by subsequent crops. However, due to the logistical obstacle of determining profile NO₃⁻-N at the farm level, a basic soil productivity approach was advocated in the present study. A yield-based N fertilizer recommendation was proposed in the present study yet needs to be further evaluated. For example, the critical value of NO₃⁻-N is variable and should be adjusted in relation to soil type and management.