Evaluating Gas Emissions from Different Feed Cropping Systems in the North China Plain: A Two-Year Field Measurement

: The cultivation of silage crops is encouraged to enhance the connection between crop and livestock production in the North China Plain (NCP). A ﬁeld experiment was designed to evaluate the ammonia (NH 3 ), nitrous oxide (N 2 O), and methane (CH 4 ) emissions of ﬁve silage cropping systems, including triticale-summer maize (Tr-SuM), triticale-spring maize (Tr-SpM), triticale-double forage maize (Tr-DFM), double forage maize (DFM), and winter wheat-summer maize (WW-SuM), as well as their biomass- and crude protein-scaled emission intensities, with respect to NH 3 and greenhouse gas (GHG). The annual nitrogen (N) emissions through NH 3 , N 2 O, and CH 4 emissions of these systems were 13.43–23.77 kg ha − 1 (4.2–5.6% of N fertilizer input), 3.43–4.56 kg ha − 1 (0.75–1.08% of N fertilizer input) and 2.10–2.85 kg ha − 1 , respectively. The total GHG emissions of these systems was dominated by the contributions of N 2 O. Ranking these systems according to their biomass and crude protein production gave Tr-DFM > DFM > WW-SuM > Tr-SuM and Tr-SpM, their partial factor productivity was in the order of Tr-DFM > WW-SuM > Tr-SuM and Tr-SpM > DFM, and the order of their emission intensity was DFM > Tr-SuM > Tr-DFM > WW-SuM > Tr-SpM. In conclusion, the Tr-DFM needs to be further investigated for its suitability in the NCP, owing to its superior productivity and moderate emission intensities.


Introduction
In China, animal production is booming to meet the increasing demand for animal products, including milk, meat, and eggs. At the same time, the unbalanced proportions of various cropping system areas need to be modified, since they partially contribute to the increasing imports of soybeans from abroad as animal feed. Therefore, adjusting the cropping systems for better animal feed production is considered necessary and imperative to realize a proper combination of crop and livestock production, which includes the requirements for new, efficient animal feed-producing cropping systems [1].
However, compiling different silage crops to form new rotation systems usually requires a re-establishment of the respective management practices (e.g., fertilization, irrigation and plowing) to improve biomass yield production [13]. As a result, the implementation of these new emerging systems may cause severe changes in the seasonal/annual gaseous emissions, introduce a high uncertainty to the local inventory of gases, and interrupt the progress of local air quality protection and the mitigation of GHG emissions [14]. Previous studies dealt with the GHG [15][16][17][18][19], NH 3 emissions from various summer-or spring-maize cropping systems [20][21][22], and triticale [23,24]. To our knowledge, however, few studies have been made within the NCP to characterize emissions from new cropping systems for silage and evaluate the emission intensity on the yield basis [25][26][27][28].
Additionally, seeking new practical approaches as alternative ways to improve biomass yield production and to concomitantly reduce GHG emissions is a challenging point [13]. In general, net GHG emissions from agricultural systems can be reduced by optimizing their management, such as by combining adopted varieties, making prudent water and N management decisions, and using the the soil tillage and residue management approach [20,29]. Although initial assessment of the new systems' performance could be estimated using the approaches of life cycle assessment (LCA), or a process-based model, such as the denitrification-decomposition model (DNDC) [30], side-by-side field experiments comparing GHG emissions among different cropping systems should still be carried out. This will accurately assess the NH 3 and GHG emissions of these new cropping systems in order to establish optimal feed cropping systems in the NCP [13,[31][32][33].
Furthermore, devising effective agriculture management strategies for mitigating climatic impacts is necessary, but requires a complete perspective of the agricultural impacts on radiative forcing [33][34][35]. In case of difficulties when comparing emissions of different cropping systems with various management practices, yield-scaled GHG intensity (GHGI) is considered suitable to evaluate the GHG emissions among different cropping systems when the management practices differ widely [14].
Therefore, this study intends to investigate the gas emissions of several silage cropping systems in comparison with the most popular winter wheat-summer maize doublecropping system in the NCP. This is to examine our hypothesis that silage cropping system might have lower GHGI than the traditional winter wheat-summer maize rotation owing to its higher productivity and shorter growing period. Their dry matter (DM) and crude protein (CP) productivities, and their DM yield-and CP yield-scaled NH 3 and GHG emission intensities are also evaluated in relation to the WW-SuM system. Since these selected crops have been well demonstrated to be suitable as silage for dairy and beef cattle, we have no further intention to evaluate their nutritional value, but only their DM and CP productivity. This will provide insightful information for establishing a good silage cropping system in the NCP.

Description of Experimental Site
The experimental site was located on the model farm of Hebei Agricultural University in Baoding, Hebei Province, North China. The regional climate was a warm-temperate monsoon climate (i.e., spring from April-May, summer from June-August, autumn from September-October, and winter from November-February). The mean annual air temperature was 12-13 • C, and the annual precipitation was approximately 550 mm, mainly occurring from June to August. The soil on the experimental site was a Eutric Cambisol on alluvial deposits; the physical and chemical properties of the experimental soil (a mixture of five sampling sites with random distribution) prior to the experiment are shown in Table 1.

Experimental Design
The field experiment was conducted from October 2015 to Sept. 2017, and included the following five silage cropping systems: (1) WW-SuM; (2) Tr-SuM; (3) Tr-SpM; (4) Tr-DFM; and (5) DFM. Each treatment had three replicates. The area of a plot was 3 m × 5 m, and the plots were randomly distributed. The varieties of summer maize and spring maize employed in this study were both zhengdan958, and the variety of winter wheat was hengmai444, triticale was Jisi#3, and forage maize was yuanyuan#1.
One rotation year is separated into 5 stages (i-v) based on the major management events in the field, such as seeding (S), fertilization (F), irrigation (I). and plowing (P) (Figure 1). The application rates of mineral N fertilizer for each treatment are shown in Table 2. The application rates of phosphorus and potassium as basal mineral fertilizers for each growing season of all crops were 80 kg P 2 O 5 ha −1 and 60 kg K 2 O ha −1 , respectively. For the basal application at the seeding stage, all fertilizers were incorporated into the soil through plowing. For topdressing the N fertilizer was surface applied, followed by an immediate flood irrigation. The scheme of the field managements in one rotation year is illustrated in Figure 1. The determination of the harvesting time of these silage crops was based on the feed quality indicators [36].

Dry Matter Yields and Nutritive Parameters
The DM yields for WW, Tr, SpM, SmM, and FM were determined. The plants were oven-dried at 75 • C after harvesting the entire plot at the optimal time, according to the feed quality indicators. The total N content of the harvested materials (N plant ) was measured using the Kjeldahl N determination procedure, and the CP contents were estimated according to Equation (1). The partial factor productivities (PFP, kg kg −1 ) of the DM (kg ha −1 ) and CP yield (kg ha −1 ) against N application were calculated using Equation (2).

Dry Matter Yields and Nutritive Parameters
The DM yields for WW, Tr, SpM, SmM, and FM were determined. The plants were oven-dried at 75 °C after harvesting the entire plot at the optimal time, according to the feed quality indicators. The total N content of the harvested materials (Nplant) was measured using the Kjeldahl N determination procedure, and the CP contents were estimated according to Equation (1). The partial factor productivities (PFP, kg kg −1 ) of the DM (kg ha −1 ) and CP yield (kg ha −1 ) against N application were calculated using Equation (2).

N2O and CH4 Measurements
The static chamber technique, consisting of a polyvinyl chloride (PVC) collar inserted into the soil 5 cm deep and a PVC cylinder cover (20 cm tall) set on the collar, was used to determine N2O and CH4 fluxes in the different rotation systems ( Figure 2). However, the CO2 fluxes in the different rotation systems were not considered in this study, mainly due to the small changes for a short period study [37]. The collar and cover were sealed with distilled water during the measurement, and the inner air samples were collected using a syringe through a medical three-valve port on the top of the cylinder cover. The gaseous emissions were measured daily for 7 days after N fertilization, was well as daily for 4 days after each irrigation or precipitation event, and were then measured every 3-7 days during the rest of the study period. Air sampling took place during 8:00-10:00 am. The covering period was 30 min, with 20 mL air samples collected from the cylinder at 0, 15, and 30 min. The soil and air temperatures were also monitored. The N2O and CH4 concentrations of the air samples were measured with a gas chromatograph (Agilent 6820, Santa Clara, CA, USA) equipped with an electron capture detector ECD (330 °C) for N2O and a flame ionization detector FID (250 °C) for CH4, and the flow  The static chamber technique, consisting of a polyvinyl chloride (PVC) collar inserted into the soil 5 cm deep and a PVC cylinder cover (20 cm tall) set on the collar, was used to determine N 2 O and CH 4 fluxes in the different rotation systems ( Figure 2). However, the CO 2 fluxes in the different rotation systems were not considered in this study, mainly due to the small changes for a short period study [37]. The collar and cover were sealed with distilled water during the measurement, and the inner air samples were collected using a syringe through a medical three-valve port on the top of the cylinder cover. The gaseous emissions were measured daily for 7 days after N fertilization, was well as daily for 4 days after each irrigation or precipitation event, and were then measured every 3-7 days during the rest of the study period. Air sampling took place during 8:00-10:00 am. The covering period was 30 min, with 20 mL air samples collected from the cylinder at 0, 15, and 30 min. The soil and air temperatures were also monitored. The N 2 O and CH 4 concentrations of the air samples were measured with a gas chromatograph (Agilent 6820, Santa Clara, CA, USA) equipped with an electron capture detector ECD (330 • C) for N 2 O and a flame ionization detector FID (250 • C) for CH 4 , and the flow rate of carrier gas was 50 mL min −1 . The flux rates of N 2 O and CH 4 were calculated using Equation (3): where F represents the flux rates of N 2 O and CH 4 (µg m −2 h −1 ), dC/dt is the slope of the gas concentrations with the sampling time (mg m −3 h −1 ), H is the height of the cylinder cover (0.20 m), T 0 is the absolute temperature (273.15 K), and T is the temperature inside the cylinder cover (K).
Atmosphere 2022, 13, 1153 where F represents the flux rates of N2O and CH4 (μg m −2 h −1 ), dC/dt is the slope of the gas concentrations with the sampling time (mg m −3 h −1 ), H is the height of the cylinder cover (0.20 m), T0 is the absolute temperature (273.15 K), and T is the temperature inside the cylinder cover (K).

NH3 Measurements
The calibrated Draeger-Tube method (DTM) was employed to measure the NH3 emissions after N fertilization ( Figure 2) [38][39][40]. The corrected NH3 concentration was calculated using Equation (4): To calculate the absolute fluxes taking the actual wind speed into account, the raw fluxes were converted into kg N ha −1 h −1 . Depending on the height of the canopy of the field, the absolute fluxes were calculated using the calibration Equation (7) or Equation

NH 3 Measurements
The calibrated Draeger-Tube method (DTM) was employed to measure the NH 3 emissions after N fertilization ( Figure 2) [38][39][40]. The corrected NH 3 concentration was calculated using Equation (4): with: F Ng , the raw NH 3 fluxes [mg N m −2 h −1 ] from the area covered by the chambers (415 cm 2 ); V, the air volume sucked through the tube; c, the corrected NH 3 concentration [ppm]; P act , the actual barometric pressure [hPa] for the pressure conversion factor; T act , the actual air temperature [ • C] for the temperature conversion factor; and t, the duration of the measurement(s).
To calculate the absolute fluxes taking the actual wind speed into account, the raw fluxes were converted into kg N ha −1 h −1 . Depending on the height of the canopy of the field, the absolute fluxes were calculated using the calibration Equation (7) or Equation (8) [39], with Equation (7) used for low canopies, such as wheat, and Equation (8) used for high canopies, such as maize fields.
ln(absolute flux

Calculation of Emission Intensities
The GHG emissions in term of the equivalent CO 2 emissions were estimated with Equations (9) and (10) using the global warming potentials of N 2 O and CH 4 over a 100-year horizon, as provided by the IPCC [41]: The indirect N 2 O emissions from the redeposited NH 3 were calculated by assuming that the redeposition of volatilized NH 3 can form an N application, as does N fertilization. Its potential emissions factor for N 2 O would be of the same magnitude as the direct emissions indicated by the IPCC [42], and it can be calculated using Equation (11): with: N 2 O ind , the indirect N 2 O emissions derived from the redeposited NH 3 (kg ha −1 ); F NH3 , the cumulative NH 3 emission (kg N ha −1 ); EF N2O , the default emissions factors in the IPCC (the value of 1.0% was used in this study); 44, the molecular weight of N 2 O (g mol −1 ); 28, the N in the molecular weight of N 2 O (g mol −1 ).
To assess the integrated greenhouse effects of different rotation systems, the annual GHG emissions (the cumulative emissions during one whole experimental year (i.e., October 2015-September 2016 and October 2016-September 2017), including the N 2 O, N 2 O ind (from the redeposition of NH 3 ), and CH 4 were used to estimate the emission intensities on the basis of DM production and CP production, respectively. However, the impacts of different rotations on the net CO 2 exchange between atmosphere and terrestrial ecosystems and the GHG emissions from the agricultural inputs such as seeds, irrigation, plowing, and fertilizers were not included.

Data Analysis
The data were statistically analyzed using Duncan's multiple range test for significant differences between treatments at p < 0.05. All the data analysis was conducted with the aid of the SPSS 22.0 software package.

DM and CP Production of Different Rotation Systems
During the experimental period of 2017-2019, the DM production of the five cropping systems ranged from 20,244 to 33,320 kg ha −1 (Table 3) (see details in Table S1). In comparison with the conventional system, WW-SuM in North China, the Tr-DFM was consistently found to have a greater DM production (by 13.2%, p < 0.05), and the other cropping systems were characterized by a significantly lower production (22.1-31.2%, p < 0.05). In addition, the CP production of the five systems varied from 1715 to 2579 kg ha −1 (Table 3) (see details in Table S2). Similarly, the Tr-DFM also consistently produced 12.1% more CP than the WW-SuM, while the other rotation systems had a 6.2-25.5% lower production than the WW-SuM. In addition, the 2-year average DM production of triticale in the Tr-SuM was 8192 kg ha −1 , 72% and 26% greater than those in the Tr-SpM and Tr-DFM rotations, respectively (Table S1). This was attributed to the difference in the number of cuttings (2 cuttings in the Tr-SuM vs 1 cutting in the Tr-SpM and Tr-DFM). Table 3. DM productions and the PFP DM (mean ± standard deviation) of different rotation systems during the experimental period.

Rotations
Mean DM (kg ha − In addition, the partial factor productivities of DM and CP production (PFP DM and PFP CP ) on the basis of per unit of N input were also examined. As shown in Table 3, the PFP DM of Tr-DFM reached 78.40 kg kg −1 and was 19.9% greater than that of the conventional WW-SuM (p < 0.05), whereas the PFP DM of Tr-SuM and Tr-SpM were significantly lower than those of the WW-SuM (p < 0.05). With respect to the PFP CP , the Tr-DFM was also characterized as having the greatest productivity and had a significantly higher value than the WW-SuM (p < 0.05) ( Table 3).
In summary, of the five cropping systems, the Tr-DFM rotation appeared to have better productivity than the conventional WW-SuM and the other alternatives.

N 2 O and CH 4 Emissions of Different Cropping Systems
The N 2 O emissions from the five cropping systems are shown in Figure 3. In general, the N 2 O emission rates usually peaked 3-4 days after N fertilization, although the peak emission rates differed among these systems due to the differences in the timing and rate of N fertilization.  (Figure 3b). In addition, due to the large differences in timing and amounts of N fertilizations (Table 2), the N 2 O emissions patterns of the five rotation systems differed, especially between the DFM and the other rotation systems. For example, there were no apparent emissions peaks in stages i and ii for the DFM, and this highlighted the importance of controlling N 2 O emissions from the DFM in the summer season ( Figure 3). In addition, the annual N 2 O emissions of the two-year average of the Tr-DFM reached 7.17 kg ha −1 , which were significantly greater than those of the other rotations, which varied between 5.31 and 5.96 kg ha −1 ( Table 4). The ratio of the annual N 2 O-N losses to their annual N application rates (AEF N2O ) were calculated to represent the relative N 2 O emissions factor. It appears that the Tr-DFM was also characterized as having the greatest AEF N2O of 1.08%, which was comparable to those of WW-SuM, Tr-SuM, and DFM (p > 0.05), but significantly higher than for Tr-SpM (p < 0.05) ( Table 4).
The measured CH 4 fluxes are shown in Figure 4. During most of the two-year experimental period, negative emissions (i.e., CH 4 uptake by soils) were observed for the five rotation systems, although the uptake varied considerably, and no consistent impact from the irrigation and N fertilization was identified. This indicated the minor role of field management practices on CH 4 emissions from the selected cropping upland systems under sub-humid climatic conditions in North China. In addition, the annual CH 4 uptake of the two-year average of the five rotation systems ranged from 2.10 to 2.85 kg ha −1 , and no significant differences were observed among them (Table 4).

NH3 Emissions of Different Rotation Systems
The NH3 emissions after N fertilization were measured in the first experimental year ( Figure 5). The NH3 emissions from WW-SuM, Tr-SuM, Tr-SpM, and Tr-DFM in stage i

NH 3 Emissions of Different Rotation Systems
The NH 3 emissions after N fertilization were measured in the first experimental year ( Figure 5). The NH 3 emissions from WW-SuM, Tr-SuM, Tr-SpM, and Tr-DFM in stage i were undetectable after basal fertilization in mid-October 2017 ( Figure 5), which might be mainly attributed to the application method of incorporation through plowing, with immediate irrigation afterwards. Nonetheless, considerable NH 3 emissions in other stages were observed when surface application methods were used. Here, the NH 3 emissions peaked 1-2 days after fertilization and started declining afterwards, although the declining trends might be disturbed by rainfall events, which might have caused short-period increases in NH 3 emissions. In general, the NH 3 emissions from these rotation systems mainly occurred within 7-10 days after N fertilization.    The NH 3 emissions from different rotation systems are shown in Table 5. The relative NH 3 -N losses with respect to their N application were also calculated as a ratio of the annual NH 3 -N losses to the annual N application rates, representing the relative NH 3 emissions factor (AEF NH3 ). Of the five systems, the DFM rotation had the lowest NH 3 emissions (p < 0.05) compared to the others, which was mainly due to the lowest total annual N application rate of 325 kg ha −1 ( Table 2). The Tr-DFM rotation had a slightly lower N rate of 425 kg ha −1 , but a slightly higher NH 3 emission in comparison with WW-SuM, Tr-SuM, and Tr-SpM, which is likely due to more application events (5 for Tr-DGM vs. 4 for the others). In addition, the AEF NH3 of Tr-DFM was significantly greater (p < 0.05) than those of other comparable crops (Table 5).

Greenhouse Gases Emissions of Different Rotation Systems
The greenhouse effects of different rotation systems, including direct (N 2 O and CH 4 ) and indirect (NH 3 ) components, expressed as CO 2 -e, are given in Tables 4 and 5. As expected, the positive CO 2 -e emissions derived from the N 2 O of different systems were found to vary from 1407 kg ha −1 in the Tr-SpM to 1900 kg ha −1 in the Tr-DFM (Table S3), and this rotation system had significantly higher emissions than the others (p < 0.05) ( Table 4). The CO 2 -e fluxes of the CH 4 of all rotation systems were negative because the soils acted as a sink for the atmospheric CH 4 , and these rotation systems showed similar results, with a narrow range from −79.8 to −58.8 kg ha −1 , although no significant differences among these systems were identified (Table 4). In addition, the indirect GHG emissions from NH 3 volatilization varied from 35.6 to 62.9 kg ha −1 and only played a minor in the total GHG emissions (Table 5). Overall, the total GHG emissions of these rotation systems were dominated by the contributions of N 2 O emissions from a regime of N 2 O, CH 4 , and NH 3 , and significantly higher emissions from the Tr-DFM were obtained (p < 0.05).

Emissions Intensities of Different Rotation Systems
Additionally, the emission intensities of CO 2 -e and NH 3 -N corresponding to the production of 1 kg CP and 1 kg DM for all rotation systems were also calculated ( Figure 6). It is found that for the emission intensities on the CP basis, the NH 3 -N intensities ranged from 7.84 g kg −1 for the DFM to 10.19 g kg −1 for the Tr-SpM, and the CO 2 -e intensities ranged from 0.65 kg kg −1 for the Tr-DFM to 0.82 kg kg −1 for the DFM, where the Tr-DFM has the lowest GHG intensity and medium NH 3 -N intensity. However, no significant difference among these cropping systems in terms of CO 2 -e and NH 3 -N can be found on the DM basis. 6). It is found that for the emission intensities on the CP basis, the NH3-N intensities ranged from 7.84 g kg −1 for the DFM to 10.19 g kg −1 for the Tr-SpM, and the CO2-e intensities ranged from 0.65 kg kg −1 for the Tr-DFM to 0.82 kg kg −1 for the DFM, where the Tr-DFM has the lowest GHG intensity and medium NH3-N intensity. However, no significant difference among these cropping systems in terms of CO2-e and NH3-N can be found on the DM basis.

Performance of Different Cropping Systems
The obtained DM amounts of forage maize in the first forage maize season were 6-59% and 140-162% greater than those in the following maize season, in the first and second experimental year, respectively (Table 3), thereby reflecting the impact of low temperatures and radiation in the second season on DM yields [27]. Meanwhile, the DM yields of the forage maize in the DFM in the two seasons appeared to be smaller than those of the Tr-DFM (Table 3), which might be attributed to the low residual effect of N fertilization due to the lack of large amounts of N fertilization when triticale production was absent [43,44]. Overall, the higher value of the Tr-DFM as a livestock feedstuff over the other rotations was mainly contributed by the double-forage maize production (Table

Performance of Different Cropping Systems
The obtained DM amounts of forage maize in the first forage maize season were 6-59% and 140-162% greater than those in the following maize season, in the first and second experimental year, respectively (Table 3), thereby reflecting the impact of low temperatures and radiation in the second season on DM yields [27]. Meanwhile, the DM yields of the forage maize in the DFM in the two seasons appeared to be smaller than those of the Tr-DFM (Table 3), which might be attributed to the low residual effect of N fertilization due to the lack of large amounts of N fertilization when triticale production was absent [43,44]. Overall, the higher value of the Tr-DFM as a livestock feedstuff over the other rotations was mainly contributed by the double-forage maize production (Table 3). A similar study assessing these forage cropping systems also indicated that the DM and the total digestible nutrients yields of the triticale-maize systems were markedly higher than those associated with conventional cultivation, when the accumulated temperature was sufficient [45]. Such phenomenon can be attributable to several factors [46]. Generally, summer maize has been demonstrated to have a greater yield gap and production gap than winter wheat, and is henceforth considered to be the most important crop in terms of increasing future grain production in the NCP [47]. However, the summer maize yield can be limited by many factors, in addition to factors such as plant density, N input, the sowing date, and potassium fertilizer input [48][49][50]; the growth of summer maize (bred for quick maturity to allow for the winter wheat to be sown in time) could be restricted due to the declining kernel filling rate during the late stage because of the low temperature and solar radiation in late September [51]. In our study, the early harvesting of triticale in mid-April in the Tr-DFM rotation extended the length of the growing season for forage maize; meanwhile, the forage maize has a shorter growing period than the conventional maize and thus, can partly avoid the low temperature period in later fall. It is concluded that with respect to feed production, the Tr-DFM rotation can make full use of the climatic resources, with a relatively high productivity in terms of DM production and partial factor productivity, but further research is needed to validate the agronomic assumptions underlying this scenario.

Gaseous Emissions
The high N 2 O and NH 3 emissions from the Tr-DFM were determined to be mainly caused by the high N fertilization in the summer, in combination with favorable conditions for gaseous emissions. The N 2 O emission peaks were mainly associated with high temperatures and high soil water content, resulting from rainfall or irrigation events [20,52]. Similar to other studies [22,53], the sums of the direct and indirect GHG emissions of all of our rotation systems were consistently dominated by N 2 O emissions, which were followed by the indirect GHG from NH 3 redeposition and the negative CH 4 fluxes. This is in agreement with the fact that the single largest source of greenhouse emissions from crop production in upland cropping systems was the emission of N 2 O [52,54]. Of the alternative cropping systems, the Tr-DFM rotation was characterized by the lowest GHG intensity and medium NH 3 -N intensity on the basis of CP ( Figure 5), mainly due to the greatest productivity (Table 3).

Implications
In this study the Tr-DFM was characterized by greater productivity over the conventional WW-SuM and other rotation systems and low or moderate yield-scaled emission intensities, and the GHG emissions were dominated by N 2 O emissions, especially during maize seasons. Consequently, from an environmental and food security perspectives, the Tr-DFM rotation should be encouraged for promoting more efficient and cleaner forage production in the NCP [55]. Therefore, the remaining concern for this rotation will be how to further reduce the absolute emissions.
First, mitigating the direct and indirect gaseous emissions by optimizing nutrient management plays an important role in lowering emission intensities. In our case, basal N fertilization in the wheat season, and all N fertilization in the maize season, are critical periods for N 2 O mitigation. It is reported that farmers in the North China Plain apply relatively high rates of N fertilizer to maize [53], thus optimizing N application rates to improve N efficiency in combination with water saving practices (e.g., drip irrigation can reduce N 2 O emissions by 32% and 46%, compared to furrow and sprinkler irrigation systems, respectively) may exhibit strong potential for reducing GHG emissions from the Tr-DFM rotation [21,56,57].
Second, the application of biochar [54,[58][59][60] and the use of manure as a substitute for chemical N have been demonstrated to be promising strategies for reducing the GHG and ensuring food security concomitantly in these intensive cropping systems in the NCP, and the application of the above practices may also be helpful for the further GHG reduction for the Tr-DFM rotation system [20,22,30,61,62]. In addition, inhibitors for urease, e.g., the novel urease inhibitor product, Limus ® (BASF, Ludwigshafen, Germany), containing active ingredients N-(n-butyl) thiophosphoric triamide (NBPT) and N-(n-propyl) thiophosphoric triamide (NPPT)) and nitrification (the 3, 4-dimethypyrazole phosphate, DMPP) could also be promising tools to mitigate N losses and N 2 O emissions from Tr-DFM rotation [63], but their impacts need to be examined with field measurements.
Third, the GHG emission intensities from agricultural systems can be kept low when the management is optimized toward better exploitation of the yield potential [52]. In this study, field management was based on the conventional practices of the local farmers. These practices pose the necessity of applying advanced management technologies in order to realize a high yield and adopting technical progress and policy support to overcome the yield bottlenecks [64,65].
For instance, many farming system models can be used to investigate the potential yield, water-limiting or nutrient-limiting yields, and the yield gaps across regions, e.g., the APSIM [66]. Taking maize as an example, contributions of the variety, sowing date, planting density, irrigation, and nitrogen fertilization to the yield gaps can be estimated and evaluated. A previous study identified that the declining radiation, together with increasing temperature, particularly during the pre-flowering period, might decrease the potential yield of maize, and accordingly, the selection of new maize varieties that can maintain the pre-flowering periods and extend post-flowering periods led to significant yield increases toward the potential yield at 7 out of the 10 sites in the NCP [60]. Therefore, making full use of these models to better integrate precipitation, irrigation, climate-resilient maize varieties, and planting density can largely improve maize yields and reduce emission intensities of the Tr-DFM rotation in the NCP [66][67][68][69].
Although this paper provided novel insights into the structural reform of agricultural cultivation from the food and environmental perspectives, long-term and comprehensive evaluation at various eco-regions of the Tr-DFM rotation is necessary in the future, which should include the GHG emissions from other agricultural inputs/managements such as seeds, irrigation, or plowing to make solid recommendation [55].

Conclusions
This field study investigated the gaseous emissions of five rotation systems over two years in the NCP. All these five rotation systems are sources of NH 3 and N 2 O, but weak sinks of atmospheric CH 4 . The total GHG emissions of these systems were dominated by the contribution of N 2 O emissions. Of the selected rotation systems, the triticale-double forage maize showed greater DM and CP production and greater partial factor productivities per kg N, but relatively low NH 3 -N and GHG emission intensities. Therefore, further research for examining the suitability of the triticale-double forage maize in the NCP and optimizing the management practices is needed.
Supplementary Materials: The following supporting information can be downloaded at: https: //www.mdpi.com/article/10.3390/atmos13071153/s1, Table S1: DM productions and the PFPDM (mean ± standard deviation) of different rotation systems during the experimental period; Table S2: CP productions and the PFP CP (mean ± standard deviation) of different rotation systems during experimental period; Table S3: GHG emissions (mean ± standard deviation) of N 2 O, CH 4 , and indirect N 2 O from the deposition of emitted NH 3 of different rotation systems during the experimental period.