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Sixteen individually subsurface drained plots (hydrologically isolated using border tiles) were established in fall 2016 at the University of Illinois Dudley Smith Farm in Christian County, IL, U.S. (39° 27' N, 89° 6' W). Each plot was approximately 0.85 ha, containing three tile laterals at 18 m spacing (Figure 1). The drainage system was design using a drainage design coefficient of 9.5 mm day⁻¹ (i.e., the rate at which water is to be removed from the field). The soils were generally silty clay loam and silt loam series, classified as somewhat poorly drained (Herrick, Oconee, and Oconee-Darmstadt-Coulterville series), poorly drained (Virden series), and moderately well-drained (Harrison series) (Web Soil Survey, 2018). The region has a hot humid continental climate (Köppen Climate Classification System: Dfa), with long term annual rainfall of 1,043 mm and annual mean temperature of 11.6°C (30-year average). Daily temperature and precipitation were recorded using an on-site weather station (HOBO RX3000, Onset Computer Corporation, Bourne, MA, U.S.) (Figure 2).

Each plot drained to an inline control structure (Agridrain^TM, Adair, IA, U.S.). Beginning in late spring 2017 (April/May), flow was continuously monitored using a water level data logger (HOBO U20L-04, Onset Corporation, Bourne, MA, U.S.; water depth recorded every 15 min) at six of the 16 plots (plots 3, 7, 9, 10, 13, and 15). These initial six plots were selected from across the site to trial potential monitoring equipment during this baseline year; all plots were eventually instrumented during the treatment period (data not presented here). Drainage flow rates were calculated using a calibrated v-notch weir equation or a compound weir equation at greater flow depths (AgriDrain^TM, personal communication; Chun and Cooke, 2008). Drainage water samples (~100 mL) were collected weekly from all 16 plots, filtered within 24 h (0.45 μm, S-Pak® Membrane Filters, Millipore Sigma, Darmstadt, Germany), and stored frozen until analysis for NO₃-N (within 20 days; method 10-107-106-1-J, Lachat QuickChem 8500 series, Loveland, CO, U.S.). Nitrate-N loads for this period were estimated by multiplying NO₃-N concentrations by discharge volumes for each sampling event and summing across the growing season. Yield-scaled NO₃-N leaching losses (YSNO₃, in kg NO₃-N per Mg of grain) were estimated by dividing NO₃-N loads by grain yield for each plot.

Measurements of N₂O were performed following the closed-static chamber method according to USDA-ARS GraceNET Project Protocols (see details in Parkin and Venterea, 2010). The chamber consisted of two parts: a chamber base (67.3 cm length × 40.6 cm width × 14 cm height) and a vented closed chamber lid (same dimensions as base) that was covered with reflective double bubble foil insulation (Ecofoil, Urbana, IA, U.S.) to minimize temperature changes during gas sampling. The lids also contained a layer of weather stripping (Lundell Manufacturing Corporation, Minneapolis, MN, U.S.) lining the connection between lids and base to create an air-tight seal during gas sampling and prevent ambient mixing. The chamber bases were inserted 5 cm into the soil on May 15, ~4.5 m beside the center tile lateral to obtain representative drainage conditions. This location was the midpoint between the plot area furthest from the lateral (9 m) and directly over the lateral. Chamber bases were left in place during the entire growing season (Figure 1).

Gas samples were collected weekly from side-dress N application until August, and twice a month thereafter. On each sampling date, the chamber lid was placed on top of the chamber base and secured in place with clamps. Each chamber lid had an airtight septum at the top through which samples were withdrawn. Individual gas samples of 20 mL were taken at 0, 16, 32, and 48 min following chamber deployment using a 20 mL syringe. After withdrawing a sample, 5 mL of gas was ejected, and 15 mL was immediately transferred into a 10 mL previously evacuated glass vial sealed with butyl rubber stoppers (Voigt Global Distribution Inc., Lawrence, KS, U.S.). Rubber stoppers were covered with clear RTV silicone adhesive sealant (Dow Corning, Midland, MI, U.S.) to prevent leakage. Gas samples were stored in glass vials until analyzed by gas chromatography (Shimadzu GC-2017, Canby, OR, U.S.). Nitrous oxide fluxes were calculated from the linear increase in gas concentration in the chamber headspace vs. time, as described by Parkin and Venterea (2010). Cumulative area-scaled N₂O emissions (cN₂O) were estimated using trapezoidal integration of flux vs. time, as described by Venterea et al. (2011). Yield-scaled N₂O emissions (YSNE, in kg N₂O per Mg of grain) were estimated for each plot by dividing cN₂O by the respective grain yield (van Groenigen et al., 2010).

Soil samples for NO₃-N and NH₄-N determination were taken following procedures described by Graham et al. (2018). Briefly, composite samples were obtained from five equally spaced soil cores across the inter-row area along a transect running perpendicular to the crop row. Samples were collected to 20 cm depth near gas chambers in each plot using a 2 cm diameter probe. Soil inorganic N was extracted within 24 h using 2M KCl and NO₃-N and NH₄-N concentrations were determined using a Smartchem 170 discrete wet chemistry auto-analyzer (Unity Scientific, Milford, MD, U.S.).

Corn was grown with uniform management across all 16 plots in 2017. Following pre-plant tillage to prepare the seed bed (S-tine field cultivator 2210 John Deere, Moline, IL, U.S.), corn was planted on April 26 2017 at 80,000 seeds ha⁻¹ and 76 cm row spacing. Nitrogen fertilizer management consisted of a pre-plant application (April 25 2017; 168 kg N ha⁻¹) and a side-dress application (June 14 2017; 135 kg N ha⁻¹), both as liquid urea ammonium nitrate (UAN) (28-0-0, N-P₂O₅-K₂O) using a coulter applicator (BLU-JET AT6020, Thurston Manufacturing Company, NE, U.S.) that injected the liquid fertilizer between crop rows at a depth of 3.5 cm below the soil surface.

Aerial imagery was collected using a UAV (3DR® Drone Site Scan, Berkeley, CA, U.S.) equipped with a multi-spectral sensor (Parrot Sequoia®, Paris, France) on June 14 2017 and July 12 2017 (corn approximately at growth stages V6 and R1, respectively). The images were taken at an altitude of 100 m, with spatial resolution of 10 cm. The Normalized Difference Vegetation Index (NDVI) and Normalized Difference Red Edge Index (NDRE) were calculated from the reflectance measurements in the Red, Red Edge, and Near Infrared (NIR) portion of the spectrum, according to the following equations (Gitelson, 2011):

A total of 20 locations over the site were randomly selected to collect plant biomass samples after the drone flight on June 14 2017. The sample areas (0.76 m²) were georeferenced using a Global Position System (GPS) (Geo 7X handheld GeoCollector^TM, Trimble®, Wesminster, CO, U.S.). The plants were clipped at ground level, dried at 60°C in a forced-air oven for 7 days, ground to pass through a 2 mm screen (Wiley Mill, Arthur H. Thomas Co., Philadelphia, PA, U.S.), and analyzed for N via combustion on an elemental analyzer (Brookside Labs, New Bremen, OH, U.S.).

After corn physiological maturity (growth stage R6), grain and biomass N concentration was determined following a standard research protocol in this region (Kitchen et al., 2017). A total of six whole plants were taken near the gas chambers within each plot and separated into ear and stover (stems + leaves) fractions. The dried stover was ground to pass through a 2 mm screen using the Wiley Mill. Corn grain was shelled from ears using an Almaco ECS (Nevada, IA, U.S.). Grain moisture and test weight were measured with a grain analyzer (Model GAC 2000, DICKEY-John Corp., Springfield, IL, U.S.). Grain yields were corrected to 155 g kg⁻¹ moisture content. To calculate total aboveground N uptake, N concentration for both grain and stover samples were determined by Brookside Labs as described above.

Corn was harvested on October 17 2017 using a John Deere Combine equipped with a GREENSTAR^TM Yield Monitor System and Yield Mapping System (John Deere, Moline, IL, U.S.). Grain yield was recorded every 3 s along with GPS location. Grain yield data consisted of 21,647 points (observations) for the entire field (41.5 ha). For each point, N content in grain was estimated using the average N concentration from the hand-harvested samples (1.4%). Nitrogen balance was estimated as an indicator of environmental loss, and was calculated by the difference between N input (fertilizer) and N output (N removed in grain) (McLellan et al., 2018).

After each drone flight, aerial images were processed and analyzed using Pix4D Software (Pix 4D S.A., Switzerland). A raster image file with a spatial resolution of 10 cm was created for both NDVI and NDRE of corn at both growth stages. All maps were created using ArcGIS (version 10.5, ESRI®, Redlands, CA, U.S.) Geospatial Analyst tool.

The pixel values from the raster files were extracted and averaged based on the measurement scale at which the different observational data were collected. For instance, the NDVI and NDRE values were extracted and averaged within each plant biomass sampling area (0.76 m²) to make inferences regarding the relationship between remote sensing indices and in-season plant N status and biomass production. Following the same logic both NDVI and NDRE values were extracted and averaged across the sampling area comprising the gas chamber (1.5 m²) in order to evaluate the relationship between N₂O emissions and remote sensing indices. Average NDVI and NDRE values were also obtained for each plot (~0.85 ha) to evaluate the relationship between NO₃-N loads and remote sensing indices.

Before yield map analysis, grain yield data was filtered to remove the extreme outliers [i.e., values outside of the mean ± 3 standard deviation (Schwalbert et al., 2018)] due to common inherent errors when the combine changed speed and direction (Simbahan et al., 2004). The final data set was normally distributed and comprised 97% of the original data (mean 13.2 Mg ha⁻¹, standard deviation 2.15 Mg ha⁻¹). A grain yield map was created in raster format by spatial interpolation of point measurements using the Inverse Distance Weighted method. A grid-cell size of 12.2 × 12.2 m was selected to reflect the width of the combine's head used for harvesting.

Correlation analyses were conducted using PROC CORR of the SAS® Software (version 9.4, SAS Institute, Cary, NC, U.S.) to evaluate the degree of association among remote sensing vegetation indices, crop, air, and water quality data. Correlations were considered significant at p < 0.1.

Compared to the 30 years average for the region, monthly precipitation in 2017 was high early in the growing season (April and May) and low throughout the remainder of the season (except July) (data not shown). Precipitation amounts in April and May were 47.7 and 18.2 mm greater than the 30 years average. Total precipitation in August and September was 9.3 and 2 compared to 71 and 82 mm for the 30 year average, respectively. In addition, a period of high daily precipitation was observed from late April to early May, with daily precipitation totals ranging from 4.5 to 41 mm (Figure 2).

The overall pattern of daily N₂O fluxes (dN₂O) during the growing season was similar among plots, despite differences in magnitude (Figure 3A). There were clear signals of increased N₂O fluxes on May 23, June 19, and July 25. For example, 5 days after UAN side-dress application (June 19), dN₂O increased from 4.9 and 4.3 to 72.3 and 81.7 g N₂O-N ha⁻¹ day⁻¹ on plots 1 and 2, respectively. Similarly, dN₂O were above 90 g N₂O-N ha⁻¹ day⁻¹ for both plots 7 and 16 on that date. Spikes in dN₂O were also seen later in the growing season (July 25), particularly on plots 1, 2, 8, and 9.

Whereas, trends in N₂O emissions were relatively consistent across plots, tile drainage NO₃-N concentrations showed much greater variability (Figure 3B). While there was a similar decreasing seasonal trend in NO₃-N concentrations over the growing season, the coefficient of variation (CV) of daily NO₃-N concentration was above 40%, despite the similar soil types, weather patterns, and consistent drainage design for this experimental site. For instance, on the first sampling date (May 2), NO₃-N concentration ranged from 2.9 (plot 11) to 16.6 mg NO₃-N L⁻¹ (plot 5), highlighting the within-field temporal and spatial variation. Elevated NO₃-N concentration also were observed during the last 2 weeks of May (May 17–30) on plots 8 and 13. Tile drainage flow stopped from July 27 to October 11, due to zero precipitation during this period (Figure 2), resulting in no samples being collected.

The temporal behavior of soil NO₃-N and NH₄-N concentrations were somewhat different from each other. Throughout the growing season, temporal variability was lower in soil NO₃-N (CV ranged from 42 to 60%) compared to NH₄-N concentration (CV ranged from 52 to 94%) (Figures 3C,D). Before UAN side-dress, soil NO₃-N concentration was greater (<70 ppm) in all plots compared to NH₄-N (<20 ppm). Yet, NH₄-N concentration rapidly increased in most of the plots after the second N fertilization event, with several spikes (>20 ppm increase) in NO₃-N concentration also being observed. For instance, NH₄-N concentration increased from approximately 5 to more than 150 ppm on plots 2, 8, and 13. In addition, NH₄-N concentration was above 50 ppm in all plots (except 7, 12, 15, and 16). Except for plot 1, soil NO₃-N and NH₄-N concentrations were lower toward the end of the growing season.

In general, higher spatial variability of both NDVI and NDRE were seen at V6 compared to when corn was at growth stage R1 (Figure 4). Across the entire field, the CV of NDVI and NDRE were 29 and 23% at V6 compared to 8 and 11% at R1, respectively. When averaged within plots, the CV ranged from 10 (plot 13) to 28% (plot 12) for NDVI at V6 compared to the range of 1 (plot 9) to 7% (plot 4) at R1. Similarly, higher CV was found on NDRE at V6 (ranging from 13 to 22%) than at R1 (ranging from 4 to 8%).

The linear regression models relating plant biomass and N content with both NDVI and NDRE showed a highly significant relationship (p < 0.001) (Figure 5). At growth stage V6, the variation in plant biomass was more strongly correlated with NDVI (R² = 0.67) compared to NDRE (R² = 0.40). Similar trends were seen when plant N content was plotted against NDVI and NDRE, with NDVI accounting for a larger proportion of variation in plant N content.

Corn grain yield was found to be highly variable both within-field and within-plots (Figure 6A). Across the entire field, mean grain yield was 13.2 Mg ha⁻¹ and the CV was 16%. When averaged within-plots, grain yield ranged from 12.8 (plot 4) to 15 Mg ha⁻¹ (plot 8), and the CV ranged from 5 (plot 7) to 17% (plot 14).

As the end-of-season N balance was estimated from grain yield and grain N concentration, the spatial variability of N balance followed a similar but inverse trend to yield. That is, areas in the field with low and high values of N balance corresponded to areas with high and low grain yields, respectively (Figure 6B). The average N balance across the whole field was 145 kg ha⁻¹ with a CV 14%. Despite high grain yields in portions of the field, there were no negative values for N balance, which ranged from 75 to 242 kg ha⁻¹.

Overall, few significant relationships were observed between vegetation indices and crop, air, and water quality data. However, NDVI at growth stage V6 was negatively correlated with N₂O losses (p < 0.1) (Table 1). Also, the correlation coefficient (R) between NDVI and N₂O losses increased as the season progressed (R = −0.44, −0.56, and −0.66 for cN₂O at growth stage V6, R1, and seasonal cN₂O, respectively). Early- and mid-season remote sensing vegetation indices were significantly correlated with corn grain yield and end-of-season N balance. Corn grain yield and N balance was positively and negatively correlated with both NDVI and NDRE at both growth stage V6 and R1.

One common theory for minimizing the risk of N losses is to increase crop productivity per unit of applied N (Snyder et al., 2009; van Groenigen et al., 2010; McLellan et al., 2018). Yet, surprisingly few studies have evaluated within-field relationships between crop yield and both N₂O emissions and N leaching losses, perhaps because these parameters are not often collected or reported for the same experiment (Omonode et al., 2017). In this study, growing season N₂O emissions and NO₃-N loads were not significantly correlated with grain yield (Table 1). While this finding is not consistent with the theory that higher yields correspond with lower environmental N losses, it nonetheless illustrates the benefits of this experimental approach for simultaneously evaluating of agronomic and environmental performance in this region.

The need to identify potential tradeoffs between crop productivity and N losses is also important from a policy perspective. There is increasing emphasis on improving N use efficiency by reducing N balance, which is proposed as a robust index of potential N losses because it is a measure of anthropogenic N supply that exceeds crop N demand (McLellan et al., 2018). As the majority of crop N uptake is concentrated in grain at the end of the season, large N balances are generally associated with high N rates and/or low yields. In this study, relatively large N balances resulted from an N rate well above regional recommendations, suggesting that a greater portion of applied N fertilizer was susceptible to losses. However, similar to yield, correlations between N balance and N₂O and NO₃-N leaching losses were not significant (Table 1). This finding differs from McLellan et al. (2018) who found a significant relationship between N balance and yield-scaled N losses using data from published studies and modeling efforts in the U.S. Corn Belt. In another meta-analysis assessing N₂O emissions in North America's corn production systems, Omonode et al. (2017) found a strong and positive relationship between N₂O losses and N balance, suggesting that management systems achieving low N balance (<60 kg N ha⁻¹) would possibly increase N use efficiency and decrease cN₂O. Generating additional empirical evidence through field-scale experiments under commercial production conditions should help scientists further evaluate and strengthen these relationships, especially if N balance is to be used in developing policies or incentive programs.

Evaluating patterns in N losses throughout the season may help elucidate potential relationships between N₂O emissions and NO₃-N leaching losses. In theory, N₂O and NO₃-N leaching losses should be related via soil N pools (Denk et al., 2017). Nitrogen fertilization is a major factor controlling N₂O production in agricultural soils because of its direct impact on soil mineral N availability (NH₄-N + NO₃-N) (Snyder et al., 2009), and N₂O emissions have been found to increase both linearly and non-linearly with N fertilizer rate (Kim et al., 2013; Decock, 2014; Shcherbak et al., 2014). In 2017, notable spikes in soil N₂O emissions occurred on several dates, with dN₂O increasing from 8 to 50 g N₂O-N ha⁻¹ day⁻¹ right after UAN side-dress application (Figure 3A). However, spikes did not always correspond with N application events, fluxes were also correlated with soil moisture (R = 0.55, p < 0.001, n = 80) and to a lesser extent soil temperature (R = 0.25, p = 0.028, n = 80). Following a similar logic as N₂O emissions, due to the high mobility of NO₃-N in the soil, tile drainage NO₃-N concentration is expected to increase after N fertilizer application, particularly if the N fertilizer source contains N in the form of NO₃-N and in years with high precipitation. However, in our study, only three plots showed an increase in tile drainage NO₃-N concentrations following the second N application event, whereas NO₃-N concentration remained relatively constant on the remaining plots (Figure 3B).

Soil N transformations following fertilizer N application events could help explain trends in N₂O and NO₃-N leaching losses. While there was a clear signal of increased soil NH₄-N after N side-dress application, this did not occur for NO₃-N concentrations (Figures 3C,D). In agricultural soils, NH₄-N concentration is generally low because it is rapidly converted to NO₃-N through the process of nitrification (Norton, 2008), as evidenced by the lower concentrations of NH₄-N compared to NO₃-N before UAN application events. Soil NO₃-N concentrations may not have increased because crop N uptake started to occur during the period of nitrification, which also corresponded with relatively few plots having increased NO₃-N concentrations in drainage following the second N application event. Several studies have emphasized the importance to synchronize soil N supply with crop N demand to improve N use efficiency and reduce N losses in croplands (Robertson and Vitousek, 2009; Snyder and Fixen, 2012). Often this corresponds to a split-application of N fertilizer: generally at planting (to ensure initial N supply) and right before the period of rapid crop growth and N uptake, which in corn is roughly between growth stages V8 and R1 (Sawyer et al., 2006). In the long-term, the unique approach in this experiment for monitoring N fluxes at the field-scale will provide a better understanding of how specific management practices (e.g., timing of N fertilizer application) may influence soil N availability, and in turn, the potential for either enhanced N₂O emissions or NO₃-N leaching losses depending on weather variability and crop growth patterns, among other factors.

Relationships between N loss pathways can also be compared across the growing season. Preliminary data from 2017 indicate that both daily (R = 0.08, p = 0.327, n = 133) and seasonal (R = 0.55, p = 0.259, n = 6) N₂O and NO₃-N leaching losses were not significantly correlated. While these results are only based on 1 year, they provide some important insights regarding temporal and spatial considerations when trying to link N₂O and NO₃-N leaching losses within a single study. First, there was an important temporal disconnect when N₂O vs. NO₃-N losses primarily occurred. On average, ~96 and 86% of the seasonal NO₃-N leaching and N₂O losses occurred between April and May, and between May and August, respectively. This is consistent with other subsurface drainage work showing that the largest drainage volumes occur in the March-May timeframe (e.g., Jin and Sands, 2003), which is often a period of high precipitation coupled with N fertilizer application in corn-based cropping systems. Our results are also relatively consistent with the period of highest N₂O emissions in the Midwest, with approximately 50–80% of the seasonal cN₂O occurring within 30–40 days following N application early in the growing season (Omonode et al., 2017), when plant N uptake is relatively low and excess N becomes available for nitrification and denitrification. In our study, ~42% of the seasonal cN₂O occurred within 40 days after UAN side-dress on June 14.

In this sense, the lack of a relationship between N₂O and NO₃-N leaching losses is not surprising due to the temporal difference of when these losses were occurring and the soil and climate conditions influencing those losses. However, in other years where warm, wet springs are followed by cool, dry summers, it would not be surprising if this resulted in high NO₃-N losses but low N₂O emissions. It is also important to highlight that the seasonal N losses measured here correspond to the corn growing season (April–October), and therefore do not reflect annual losses. To account for these limitations mentioned above, both N₂O and NO₃-N leaching losses will be monitored throughout the year in all 16 experimental units, which will also lead to better estimations of total N losses. Drainage events and N₂O fluxes during the winter by freeze/thaw cycles have been shown in separate studies to contribute significantly to the total N losses in certain locations and years (Christianson and Harmel, 2015b; Wagner-Riddle et al., 2017).

Beyond the temporal disconnect discussed above, there is an important spatial disconnect (i.e., measurement footprint) that may pose challenges in trying to develop quantitative relationships between N₂O and NO₃-N leaching losses. The different scale of measurements between N₂O and NO₃-N, and the within-plot variability that is likely observed for N₂O emissions in large-scale research, complicates any assessment of the relationship between these two variables. It has long been recognized that there is large spatial variability in soil N₂O emissions. Recent studies have shown that hotspots of N₂O emissions within field can account for as much as 30% of the cumulative emissions (Turner et al., 2016). While new measurement techniques are available to analyze emissions in large plots [e.g., see methods in Hensen et al. (2013)], they are considerably more expensive and may not support replicated treatment comparisons. Hence, new approaches may be needed to strengthen our ability to capture the spatial variability in soil N₂O emissions, specifically for plot sizes typical for assessing tile drainage nutrients concentrations. Recently there have been calls for not only additional field studies where multiple types of N loss pathways are simultaneously evaluated, but also for better data reporting to enhance future agro-ecosystem data syntheses and meta-analyses (Eagle et al., 2017a). A great deal of research activity is being directed toward addressing this knowledge gap, thus we encourage others to consider these temporal and spatial methodology points when evaluating both N₂O and NO₃-N leaching losses in the same study.

Despite the rapid growth of UAVs in agriculture, little work has explored the potential for new technologies to directly link sustainability outcomes with improved agronomic efficiencies. The value in the present research is not only being able to assess these relationships after harvest, but also earlier in the growing season when adaptive N management decisions could still be made. To date, we are unaware of any effort to assess the degree to which in-season measurements of crop performance or N use efficiency may correspond with environmental N losses.

Our results from one growing season show that UAV images collected at corn growth stage V6 may be an indicator of N₂O losses, but not for NO₃-N leaching losses (Table 1). Vegetation indices such as NDVI have been extensively used to make inferences of in-season plant N status and biomass production, and generally, greater leaf area and greener plant biomass result in higher NDVI values (Rembold et al., 2013) (Figure 5). In theory, areas in the field with low early-season NDVI values correspond to areas with poor crop establishment and consequently low N uptake, and with more N accumulating in soil, it becomes susceptible for losses through denitrification. This rationale could help explain the strong and negative relationship between early-season NDVI and N₂O losses found in this study. In addition, the correlation coefficient between early-season NDVI and N₂O losses increased as the season progressed (R = −0.44, −0.56, and −0.66 for cN₂O at growth stage V6, R1, and seasonal cN₂O, respectively). On average, ~27 and 44% of the total N₂O losses had already occurred at growth stage V6 and R1, respectively. These results indicate that UAV platforms could represent an integrative tool for linking crop performance and air quality outcomes, but further research is necessary. Agricultural monitoring systems that provide timely and accurate information are of great interest to agricultural producers, allowing them to make in-season management decisions to enhance the efficiency of production. If relationships between N₂O emissions and NDVI were consistent under a wide range of conditions, such an approach could have the co-benefit of enhancing the sustainability of food production.

The correlation between remote sensing vegetation indices and NO₃-N leaching losses was not significant at any time throughout the growing season (Table 1). In fact, due to the temporal disconnect discussed above (i.e., 73% of the seasonal NO₃-N leaching losses occurred before crop emergence), this correlation was not expected to be significant. However, there might be cases where this relationship is observable, particularly if excess rainfall affects crop growth and losses during the period of crop growth contributing significantly to seasonal NO₃-N loads. In theory, it is possible that in years with significant flooding events, crop emergence/establishment would be poor (which is associated with NDVI/NDRE) and NO₃-N leaching losses would he high. Following similar logic as N₂O emissions discussed above, being able to link agronomic and environmental performance early in the growing season would provide enhanced and timely information for monitoring, measurement, and management to achieve both production and environmental goals. Nonetheless, because the majority of NO₃-N leaching on an annual basis occurs before UAVs are used to map early season crop N status, there are likely inherent limitations in using remote sensing technologies as an indicator of water quality outcomes.

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.