Spatial Variability in Inorganic Soil Nitrogen Production in a Mixed-Vegetation Urban Landscape

Urban landscapes are not homogeneous, and small-scale variations in plant community or management inputs can give rise to a large range of environmental conditions. In this paper, we investigated the small-scale variability of soil nitrogen (N) properties in a single urban landscape that has distinctly different patches or types of cover. We specifically measured soil net N mineralization, nitrification, and exchangeable forms of inorganic N for patches with traditional turfgrass versus patches with common turfgrass alternatives such as ornamental grasses, groundcovers, and mulches. All soil N properties were variable among landscape patches, showing that soil N processing can vary on scales of a few meters. Notably, both mineralization and nitrification were the highest in a patch covered with perennial peanut, but exchangeable nitrate (NO3) was low for the same soil, indicating that soils under perennial peanut may be producing high levels of inorganic N but that the produced N does not stay in the soil, possibly leaching to underlying groundwater. We recommend future studies on the mechanisms that drive the variable N properties seen under distinct urban landscape patches, with special emphasis on potential patterns in N losses for mixed-vegetation landscapes.


Introduction
A well-managed, aesthetically pleasing landscape is associated with wellbeing in many residential landscapes, and the area of turfgrass in the United States is larger than that for any irrigated crop [1]. For many urban homeowners in the United States, turfgrass is the predominant lawn cover. To maintain a healthy, attractive turfgrass cover, regular fertilization, irrigation, and pest control management plan is often established [2]. Besides the associated economic implications, the fate and potential loss of nutrients (nitrogen and phosphorus) from fertilized turfgrass have important implications for aquatic ecosystems since nutrients mobilized by leaching and/or runoff may impair receiving waterbodies through eutrophication and algal proliferation [3][4][5].
While numerous studies have indicated that nutrient losses via leaching and runoff are minimal from healthy, properly maintained turfgrass and that turfgrass lawns are sinks of nitrogen (N) in urban watersheds [6][7][8], turfgrass fertilizers are increasingly targeted by management practices and policies aimed at reducing anthropogenic nutrient inputs to aquatic ecosystems [9]. For example, in Florida, more than 50 counties and municipalities have enacted fertilizer ordinances that often prohibit any application of N-and phosphorus (P)-bearing fertilizers to urban lawns during Florida's summer rainy season (June to September) each year [10,11]. The premise behind these bans is that summer rains may lead to increased leaching and runoff losses of N and P applied as fertilizer to lawns, in turn leading to increased anthropogenic nutrient loading to nearby waterbodies. To date, the efficacy of the fertilizer ban ordinances has not been demonstrated, and they remain controversial strategies for urban nutrient management [12,13]. To address urban nutrient management needs, we need not only more studies on the mechanisms and extent of nutrient mobilization from urban landscapes but also a better understanding of soil nutrient dynamics in these landscapes [14,15]. Nutrients associated with soil organic matter pools have been identified as one source of N and P that may be mobilized from urban lawns to stormwater runoff [5,16,17]. We also need research focused on a wider variety of potential urban landscape covers, such as mulches or ornamental plants other than turfgrass. Only a few studies have investigated differences in soil nutrient cycling between turfgrass monoculture lawns and lawns with a mix of species. In one such study, Erickson et al. [8] compared N leaching and runoff from a St. Augustine turfgrass monoculture versus a mixed-species lawn in Florida. For both lawn types, N losses via surface runoff were minimal, but leaching losses were substantial, especially for the mixed-species lawns, which lost up to 48.3 kg N ha −1 via leaching. By comparison, the turfgrass lawns in the study lost 4.1 kg N ha −1 via leaching, indicating that the turfgrass was more effective than mixed-species vegetation for preventing N leaching from lawns. In another study, Amador et al. [18], studied pore water nitrate (NO 3 − ) concentrations at 60 cm soil depth under turfgrass versus various landscape covers, including flowers, shrubs, and unplanted mulched beds. In their study, flowers, managed turfgrass, and ornamental deciduous and evergreen trees represented a lower risk of NO 3 − loss from the soil than unplanted mulched areas, which the authors recommended should be used sparingly in urban landscapes because of the potential for NO 3 − leaching to groundwater. Amador et al. [18] suggested that these unplanted mulched areas were more susceptible to NO 3 − leaching because there was no plant sink for N produced by mineralization of soil organic N. That study also noted that unplanted mulched landscape beds lost via leaching nearly twice the NO 3 − input to the landscape through atmospheric deposition, making the unplanted mulched areas net sources of NO 3 − to the underlying groundwater. The sparse studies on soil N dynamics in mixed-species urban landscapes are in line with the framework for urban soil ecology presented by Byrne [19], in which the heterogeneity commonly found in urban landscapes gives rise to a specific "habitat structure," or a unique composition of physical matter with consequent unique effects on local ecological variables. Variation in habitat structure gives rise to differences in soil pH, moisture content, microbial populations, temperature, and vegetation cover, which in turn may all cause variations in the N cycling processes within an urban landscape [15,[20][21][22]. This means that distinct patches may emerge, creating a landscape mosaic where ecological variables can vary at scales of just a few meters or less. In this study, we selected a mixed-species urban landscape with this type of small-scale patchiness in vegetative cover and investigated the spatial variability of inorganic N production in soils. We hypothesized that differences in landscape cover at a spatial scale of meters would result in varying levels of soil inorganic N production, as measured by nitrification and net N mineralization rates. We tested this hypothesis by evaluating N cycling processes in soils under traditional turfgrass and several common ornamental alternatives to turfgrass.
This work is important because it helps constrain and fill knowledge gaps related to N cycling processes in urban soils by focusing on small-scale differences that are common in urban landscapes. While previous studies mentioned above [8,18] have focused solely on N leaching from mixed-vegetation landscapes, this work adds the body of knowledge by focusing on N cycling processes, namely mineralization, and nitrification. Typically, urban lawns and other green spaces are broadly categorized as "lawn" or "turfgrass," when in reality, they are seldom turfgrass monocultures but instead a mosaic of various vegetative types and ground covers. As we grapple with water quality degradation associated with excess nutrients from urban landscapes, research models may be used to predict the transformations and movement of N in urban soils-and accounting for the expected mosaic of variable N processing in urban soils can lead to improvements in those modeling efforts. For example, in Florida, the Nitrogen Source Inventory and Loading Tool (NSILT) is a model used to predict the fate of fertilizer N applied to urban landscapes. The model is based on the best available data on N inputs and N transformations in urban soils but is informed only by data on N cycling in turfgrass soils, without consideration for other land cover types (e.g., flower beds or mulched areas) [23]. In this work, we show how N cycling processes in a single urban landscape can be highly variable, and we argue that efforts to constrain the fate of urban nutrient sources can be improved by greater attention to mixed-vegetation landscape scenarios as well as data at finer spatial scales.

Study Site
The research was carried out at the University of Florida's Gulf Coast Research and Education Center (UF-GCREC) in Hillsborough County, Florida (27 • 45 39.2 N 82 • 13 47.4 W), which is part of the Tampa metropolitan area. The research center was constructed in 2005 on abandoned citrus farmland. Its main building was surrounded by a variety of ornamental vegetation cover that is typical of urban residential and commercial land uses in the Tampa, Florida area, including turfgrass, landscape trees, and flowering shrubs in mulched beds. The annual average precipitation of the site was 1325 mm, and the annual temperature ranged from 11-32 • C. The soils at the research center were mostly sandy spodosols of the Zolfo series (sandy, siliceous, hyperthermic oxyaquic Alorthods) [24].

Selection of Landscape Patches and Soil Sampling
We selected 6 distinct urban landscape patches surrounding UF-GCREC and 1 remnant agricultural (Agr) patch for soil sampling and analysis of inorganic N production ( Table 1). The non-agricultural patches were turfgrass (TfGr) and potential turfgrass alternatives common for residential landscapes in Florida, which included 1 patch of perennial peanut (PP), a low-growing alternative ground cover; 2 patches with ornamental grasses and shrubs (OMx and OGa); and 2 patches consisting mostly of mulch with little or no other vegetation (MulP and MulC). Table 1 describes the vegetation and other characteristic features of each landscape patch. The model is based on the best available data on N inputs and N transformatio soils but is informed only by data on N cycling in turfgrass soils, without co for other land cover types (e.g., flower beds or mulched areas) [23]. In this wo how N cycling processes in a single urban landscape can be highly variable, a that efforts to constrain the fate of urban nutrient sources can be improved attention to mixed-vegetation landscape scenarios as well as data at finer spa

Study Site
The research was carried out at the University of Florida's Gulf Coast R Education Center (UF-GCREC) in Hillsborough County, Florida (27°45′39.2″ N W), which is part of the Tampa metropolitan area. The research center was co 2005 on abandoned citrus farmland. Its main building was surrounded by ornamental vegetation cover that is typical of urban residential and commerc in the Tampa, Florida area, including turfgrass, landscape trees, and flowerin mulched beds. The annual average precipitation of the site was 1325 mm, and temperature ranged from 11-32 °C. The soils at the research center were m spodosols of the Zolfo series (sandy, siliceous, hyperthermic oxyaquic Alorth

Selection of Landscape Patches and Soil Sampling
We selected 6 distinct urban landscape patches surrounding UF-GCREC nant agricultural (Agr) patch for soil sampling and analysis of inorganic N ( Table 1). The non-agricultural patches were turfgrass (TfGr) and potential ternatives common for residential landscapes in Florida, which included 1 p ennial peanut (PP), a low-growing alternative ground cover; 2 patches with grasses and shrubs (OMx and OGa); and 2 patches consisting mostly of mulc or no other vegetation (MulP and MulC). Table 1 describes the vegetation and acteristic features of each landscape patch. The model is based on the best available data on N inputs and N transformati soils but is informed only by data on N cycling in turfgrass soils, without co for other land cover types (e.g., flower beds or mulched areas) [23]. In this wo how N cycling processes in a single urban landscape can be highly variable, a that efforts to constrain the fate of urban nutrient sources can be improved attention to mixed-vegetation landscape scenarios as well as data at finer spa

Study Site
The research was carried out at the University of Florida's Gulf Coast R Education Center (UF-GCREC) in Hillsborough County, Florida (27°45′39.2″ N W), which is part of the Tampa metropolitan area. The research center was co 2005 on abandoned citrus farmland. Its main building was surrounded by ornamental vegetation cover that is typical of urban residential and commerc in the Tampa, Florida area, including turfgrass, landscape trees, and floweri mulched beds. The annual average precipitation of the site was 1325 mm, and temperature ranged from 11-32 °C. The soils at the research center were m spodosols of the Zolfo series (sandy, siliceous, hyperthermic oxyaquic Alorth

Selection of Landscape Patches and Soil Sampling
We selected 6 distinct urban landscape patches surrounding UF-GCREC nant agricultural (Agr) patch for soil sampling and analysis of inorganic N ( Table 1). The non-agricultural patches were turfgrass (TfGr) and potential ternatives common for residential landscapes in Florida, which included 1 p ennial peanut (PP), a low-growing alternative ground cover; 2 patches with grasses and shrubs (OMx and OGa); and 2 patches consisting mostly of mulc or no other vegetation (MulP and MulC). Table 1 describes the vegetation and acteristic features of each landscape patch. The model is based on the best available data on N inputs and N transformati soils but is informed only by data on N cycling in turfgrass soils, without co for other land cover types (e.g., flower beds or mulched areas) [23]. In this wo how N cycling processes in a single urban landscape can be highly variable, a that efforts to constrain the fate of urban nutrient sources can be improved attention to mixed-vegetation landscape scenarios as well as data at finer spa

Study Site
The research was carried out at the University of Florida's Gulf Coast R Education Center (UF-GCREC) in Hillsborough County, Florida (27°45′39.2″ N W), which is part of the Tampa metropolitan area. The research center was co 2005 on abandoned citrus farmland. Its main building was surrounded by ornamental vegetation cover that is typical of urban residential and commerc in the Tampa, Florida area, including turfgrass, landscape trees, and flowerin mulched beds. The annual average precipitation of the site was 1325 mm, and temperature ranged from 11-32 °C. The soils at the research center were m spodosols of the Zolfo series (sandy, siliceous, hyperthermic oxyaquic Alorth

Selection of Landscape Patches and Soil Sampling
We selected 6 distinct urban landscape patches surrounding UF-GCREC nant agricultural (Agr) patch for soil sampling and analysis of inorganic N ( Table 1). The non-agricultural patches were turfgrass (TfGr) and potential ternatives common for residential landscapes in Florida, which included 1 p ennial peanut (PP), a low-growing alternative ground cover; 2 patches with grasses and shrubs (OMx and OGa); and 2 patches consisting mostly of mulc or no other vegetation (MulP and MulC). Table 1 describes the vegetation and acteristic features of each landscape patch. The model is based on the best available data on N inputs and N transformati soils but is informed only by data on N cycling in turfgrass soils, without co for other land cover types (e.g., flower beds or mulched areas) [23]. In this wo how N cycling processes in a single urban landscape can be highly variable, a that efforts to constrain the fate of urban nutrient sources can be improved attention to mixed-vegetation landscape scenarios as well as data at finer spa

Study Site
The research was carried out at the University of Florida's Gulf Coast R Education Center (UF-GCREC) in Hillsborough County, Florida (27°45′39.2″ N W), which is part of the Tampa metropolitan area. The research center was co 2005 on abandoned citrus farmland. Its main building was surrounded by ornamental vegetation cover that is typical of urban residential and commerc in the Tampa, Florida area, including turfgrass, landscape trees, and floweri mulched beds. The annual average precipitation of the site was 1325 mm, and temperature ranged from 11-32 °C. The soils at the research center were m spodosols of the Zolfo series (sandy, siliceous, hyperthermic oxyaquic Alorth

Selection of Landscape Patches and Soil Sampling
We selected 6 distinct urban landscape patches surrounding UF-GCREC nant agricultural (Agr) patch for soil sampling and analysis of inorganic N ( Table 1). The non-agricultural patches were turfgrass (TfGr) and potential ternatives common for residential landscapes in Florida, which included 1 p ennial peanut (PP), a low-growing alternative ground cover; 2 patches with grasses and shrubs (OMx and OGa); and 2 patches consisting mostly of mulc or no other vegetation (MulP and MulC). Table 1 describes the vegetation and acteristic features of each landscape patch. Soil sampling took place on each landscape patch in September 2018. We auger to take 5 cm-diameter cores from 4 random locations within each patc of approximately 52 cm. All 4 cores for each patch were then each divided int ples by depth (0-15 cm, 15-30 cm, and 30-52 cm) to provide 4 field replica depth per landscape patch. Subsamples of the soils were then air dried and sie a standard #10 (2 mm) sieve and analyzed for soil pH, total soil N, and tota pH was measured with a soil:water 1:2 (w/v) slurry. Total soil N and C were m a Thermo Flash 1112 A NC Soil Analyzer in the University of Florida Wetl chemistry Laboratory. Field moist sieved soils were used to analyze for soil water content, percent organic matter, and exchangeable inorganic N. Perc matter was determined via the loss on ignition method. Exchangeable inorga and NH4 + ) was determined by extracting 10 g soil with 50 mL 2 M KCl for 1 h ing for NO3 − and NH4 + via a continuous segmented flow analyzer (AA3, SEA quon, WI, USA) by EPA methods 353.2 and 350.1, respectively.

Inorganic Soil Nitrogen Production
We defined inorganic N production as the rates of production of NH4-N tion) and NO3-N (nitrification). Mineralization is the microbial process wher N is converted to mineral N, while nitrification is the process whereby amm converted to NO3 − N by aerobic bacteria. Both soil net mineralization and nitrif were determined after methods described by Raciti et al. [15]. Briefly, 10 g fie was incubated in Erlenmeyer flasks for 14 days with a 12:12 light/dark cycl ambient temperature (approximately 22 °C). Flasks were loosely covered wi and DI water (< 2 mL) was periodically added to the soils as needed to m capacity moisture conditions during the incubation. At the conclusion of th period, soils were extracted with 50 mL 2 M KCl and analyzed for NO3 − and NH A separate set of flasks and soils was likewise analyzed but without incubatio as the time zero, or initial, measurements. At the conclusion of the incubation mineralization was calculated as the accumulation of total inorganic N (NH4 + nitrification was calculated as the accumulation of NO3 − . Results were expres kg soil −1 day −1 , after using the initial gravimetric soil water content to base cal the equivalent dry mass of soil in each flask. Results were examined for eac patch by depth as well as on a whole-core basis [15]. Soil sampling took place on each landscape patch in September 2018. We auger to take 5 cm-diameter cores from 4 random locations within each patc of approximately 52 cm. All 4 cores for each patch were then each divided int ples by depth (0-15 cm, 15-30 cm, and 30-52 cm) to provide 4 field replica depth per landscape patch. Subsamples of the soils were then air dried and sie a standard #10 (2 mm) sieve and analyzed for soil pH, total soil N, and tota pH was measured with a soil:water 1:2 (w/v) slurry. Total soil N and C were m a Thermo Flash 1112 A NC Soil Analyzer in the University of Florida Wetl chemistry Laboratory. Field moist sieved soils were used to analyze for soil water content, percent organic matter, and exchangeable inorganic N. Perc matter was determined via the loss on ignition method. Exchangeable inorga and NH4 + ) was determined by extracting 10 g soil with 50 mL 2 M KCl for 1 h ing for NO3 − and NH4 + via a continuous segmented flow analyzer (AA3, SEA quon, WI, USA) by EPA methods 353.2 and 350.1, respectively.

Inorganic Soil Nitrogen Production
We defined inorganic N production as the rates of production of NH4-N tion) and NO3-N (nitrification). Mineralization is the microbial process wher N is converted to mineral N, while nitrification is the process whereby amm converted to NO3 − N by aerobic bacteria. Both soil net mineralization and nitrif were determined after methods described by Raciti et al. [15]. Briefly, 10 g fie was incubated in Erlenmeyer flasks for 14 days with a 12:12 light/dark cycl ambient temperature (approximately 22 °C). Flasks were loosely covered wi and DI water (< 2 mL) was periodically added to the soils as needed to m capacity moisture conditions during the incubation. At the conclusion of the period, soils were extracted with 50 mL 2 M KCl and analyzed for NO3 − and NH A separate set of flasks and soils was likewise analyzed but without incubatio as the time zero, or initial, measurements. At the conclusion of the incubation mineralization was calculated as the accumulation of total inorganic N (NH4 + nitrification was calculated as the accumulation of NO3 − . Results were expres kg soil −1 day −1 , after using the initial gravimetric soil water content to base cal the equivalent dry mass of soil in each flask. Results were examined for eac patch by depth as well as on a whole-core basis [15]. Soil sampling took place on each landscape patch in September 2018. We auger to take 5 cm-diameter cores from 4 random locations within each patc of approximately 52 cm. All 4 cores for each patch were then each divided int ples by depth (0-15 cm, 15-30 cm, and 30-52 cm) to provide 4 field replica depth per landscape patch. Subsamples of the soils were then air dried and sie a standard #10 (2 mm) sieve and analyzed for soil pH, total soil N, and tota pH was measured with a soil:water 1:2 (w/v) slurry. Total soil N and C were m a Thermo Flash 1112 A NC Soil Analyzer in the University of Florida Wetl chemistry Laboratory. Field moist sieved soils were used to analyze for soil water content, percent organic matter, and exchangeable inorganic N. Per matter was determined via the loss on ignition method. Exchangeable inorga and NH4 + ) was determined by extracting 10 g soil with 50 mL 2 M KCl for 1 h ing for NO3 − and NH4 + via a continuous segmented flow analyzer (AA3, SEA quon, WI, USA) by EPA methods 353.2 and 350.1, respectively.

Inorganic Soil Nitrogen Production
We defined inorganic N production as the rates of production of NH4-N tion) and NO3-N (nitrification). Mineralization is the microbial process wher N is converted to mineral N, while nitrification is the process whereby amm converted to NO3 − N by aerobic bacteria. Both soil net mineralization and nitrif were determined after methods described by Raciti et al. [15]. Briefly, 10 g fie was incubated in Erlenmeyer flasks for 14 days with a 12:12 light/dark cycl ambient temperature (approximately 22 °C). Flasks were loosely covered w and DI water (< 2 mL) was periodically added to the soils as needed to m capacity moisture conditions during the incubation. At the conclusion of th period, soils were extracted with 50 mL 2 M KCl and analyzed for NO3 − and NH A separate set of flasks and soils was likewise analyzed but without incubatio as the time zero, or initial, measurements. At the conclusion of the incubation mineralization was calculated as the accumulation of total inorganic N (NH4 + nitrification was calculated as the accumulation of NO3 − . Results were expres kg soil −1 day −1 , after using the initial gravimetric soil water content to base cal the equivalent dry mass of soil in each flask. Results were examined for eac patch by depth as well as on a whole-core basis [15].

•
Fallow agricultural pasture used 6 months earlier for strawberry production • Selected to provide a contrast comparison of N between residential landscapes and a remnant agricultural field Soil sampling took place on each landscape patch in September 2018. We used a hand auger to take 5 cm-diameter cores from 4 random locations within each patch to a depth of approximately 52 cm. All 4 cores for each patch were then each divided into 3 subsamples by depth (0-15 cm, 15-30 cm, and 30-52 cm) to provide 4 field replicates for each depth per landscape patch. Subsamples of the soils were then air dried and sieved through a standard #10 (2 mm) sieve and analyzed for soil pH, total soil N, and total soil C. Soil pH was measured with a soil:water 1:2 (w/v) slurry. Total soil N and C were measured on a Thermo Flash 1112 A NC Soil Analyzer in the University of Florida Wetland Biogeochemistry Laboratory. Field moist sieved soils were used to analyze for soil gravimetric water content, percent organic matter, and exchangeable inorganic N. Percent organic matter was determined via the loss on ignition method. Exchangeable inorganic N (NOx and NH 4 + ) was determined by extracting 10 g soil with 50 mL 2 M KCl for 1 h and analyzing for NO 3 − and NH 4 + via a continuous segmented flow analyzer (AA3, SEAL Inc., Mequon, WI, USA) by EPA methods 353.2 and 350.1, respectively.

Inorganic Soil Nitrogen Production
We defined inorganic N production as the rates of production of NH 4 -N (mineralization) and NO 3 -N (nitrification). Mineralization is the microbial process whereby organic N is converted to mineral N, while nitrification is the process whereby ammonium N is converted to NO 3 − N by aerobic bacteria. Both soil net mineralization and nitrification rates were determined after methods described by Raciti et al. [15]. Briefly, 10 g field moist soil was incubated in Erlenmeyer flasks for 14 days with a 12:12 light/dark cycle and at lab ambient temperature (approximately 22 • C). Flasks were loosely covered with parafilm, and DI water (<2 mL) was periodically added to the soils as needed to maintain field capacity moisture conditions during the incubation. At the conclusion of the incubation period, soils were extracted with 50 mL 2 M KCl and analyzed for NO 3 − and NH 4 + as above. A separate set of flasks and soils was likewise analyzed but without incubation and taken as the time zero, or initial, measurements. At the conclusion of the incubation period, net mineralization was calculated as the accumulation of total inorganic N (NH 4 + + NO 3 − ) and nitrification was calculated as the accumulation of NO 3 − . Results were expressed in mg N kg soil −1 day −1 , after using the initial gravimetric soil water content to base calculations on the equivalent dry mass of soil in each flask. Results were examined for each landscape patch by depth as well as on a whole-core basis [15].

Statistical Analysis
Descriptive statistics to relate mean, median, and standard errors for rates of inorganic N production were developed for each landscape patch with JMP v.15 software (SAS Institute, Inc., Cary, NC, USA). Regression analysis was used to examine possible linear relationships between mineralization and nitrification rates for each landscape patch, also with JMP v.15 software.

Inorganic Soil Nitrogen Production
For all landscape patches, median whole core net mineralization and nitrification were highest in the Agr soils, with median rates of 1.1 mg and 0.7 mg N kg/d, respectively ( Figure 1; Table S2, Supplementary Materials). Whole core net mineralization and nitrification were next highest in the PP soils (median 0.8 and 0.5 mg N kg/d, respectively). The relatively high inorganic N production rate results for the PP patch could be related to the ability of perennial peanut to fix atmospheric N in the soil in the presence of rhizobia bacteria [25]. In the process of N fixation, atmospheric dinitrogen is cleaved and enzymatically catalyzed to produce two molecules of ammonia, leading to subsidies of NH 4 + to the soil. When soil NH 4 + levels are initially low, net mineralization is slow because inorganic N is preferentially incorporated into microbial biomass [26]. On the other hand, increasing levels of soil NH 4 + have been shown to increase N mineralization rates in soils [26]. In this way, it is likely that N fixation by the perennial peanut led to high initial levels of soil NH 4 + , which in turn promoted the high N mineralization rates seen in the PP soil. We are aware of no studies on the fate of fixed N when perennial peanut is used as a turfgrass alternative in urban landscapes. However, as discussed below, exchangeable NO 3 − was lower in the PP soils than all other landscape patches, indicating that even though the PP soils had high levels of NO 3 − production (nitrification), they were not maintaining high NO 3 − levels. Potential fates of the produced NO 3 − to explain its loss in the PP soils include denitrification, plant uptake, and leaching. The well-oxygenated and low organic matter conditions of our sandy soils make denitrification unlikely, since denitrification requires oxygen-limited environments and an organic carbon source [27]. We recommend future studies to investigate whether the inorganic N produced in soils under perennial peanut is readily lost via leaching, especially in sandy soils where NO 3 − mobility would be high. While perennial peanut offers water-saving advantages over traditional turfgrass [28], it may come with the tradeoff of greater inorganic N leaching potential, though this has not been studied yet for urban soils.

Statistical Analysis
Descriptive statistics to relate mean, median, and standard errors for rates of inorganic N production were developed for each landscape patch with JMP v.15 software (SAS Institute, Inc., Cary, NC, USA). Regression analysis was used to examine possible linear relationships between mineralization and nitrification rates for each landscape patch, also with JMP v.15 software.

Inorganic Soil Nitrogen Production
For all landscape patches, median whole core net mineralization and nitrification were highest in the Agr soils, with median rates of 1.1 mg and 0.7 mg N kg/d, respectively ( Figure 1; Table S2, Supplementary Materials). Whole core net mineralization and nitrification were next highest in the PP soils (median 0.8 and 0.5 mg N kg/d, respectively). The relatively high inorganic N production rate results for the PP patch could be related to the ability of perennial peanut to fix atmospheric N in the soil in the presence of rhizobia bacteria [25]. In the process of N fixation, atmospheric dinitrogen is cleaved and enzymatically catalyzed to produce two molecules of ammonia, leading to subsidies of NH4 + to the soil. When soil NH4 + levels are initially low, net mineralization is slow because inorganic N is preferentially incorporated into microbial biomass [26]. On the other hand, increasing levels of soil NH4 + have been shown to increase N mineralization rates in soils [26]. In this way, it is likely that N fixation by the perennial peanut led to high initial levels of soil NH4 + , which in turn promoted the high N mineralization rates seen in the PP soil. We are aware of no studies on the fate of fixed N when perennial peanut is used as a turfgrass alternative in urban landscapes. However, as discussed below, exchangeable NO3 − was lower in the PP soils than all other landscape patches, indicating that even though the PP soils had high levels of NO3 − production (nitrification), they were not maintaining high NO3 − levels. Potential fates of the produced NO3 − to explain its loss in the PP soils include denitrification, plant uptake, and leaching. The well-oxygenated and low organic matter conditions of our sandy soils make denitrification unlikely, since denitrification requires oxygen-limited environments and an organic carbon source [27]. We recommend future studies to investigate whether the inorganic N produced in soils under perennial peanut is readily lost via leaching, especially in sandy soils where NO3 − mobility would be high. While perennial peanut offers water-saving advantages over traditional turfgrass [28], it may come with the tradeoff of greater inorganic N leaching potential, though this has not been studied yet for urban soils.  After Agr and PP, the TfGr soils had the third highest median rates of net N mineralization and nitrification (Figure 1; Table S2). There were likely fertilizer subsidies of inorganic N in both the Agr and TfGr patches. As with the PP soils, relatively high initial levels of inorganic N for Agr and TfGr probably led to higher inorganic N production rates during the soil incubations when compared to non-perennial peanut turfgrass alternatives (OMx, Oga, MulP, and MulC patches) [26]. For all landscape patches except the mulched areas (MulP and MulC), regression analysis revealed a significant linear relationship between nitrification and net mineralization on a whole-core basis (Figure 2). This is not surprising since nitrifying bacteria need ammonia as an energy source thus that nitrification generally increases with increasing ammonia levels in soils [27]. Identifying the underlying mechanism responsible for the lack of this relationship under the mulched landscape areas was beyond the scope of this paper, but factors that may inhibit nitrification include soil C:N ratios above~22, acid soil pH conditions, and low oxygen availability [15]. We observed that the MulP landscape patch had the highest C:N among all landscape types (~22-23, Table S1), possibly indicating suppressed nitrification and a relatively less active N cycling microbial community in the MulP soils.
After Agr and PP, the TfGr soils had the third highest median rates of net N mineralization and nitrification (Figure 1; Table S2). There were likely fertilizer subsidies of inorganic N in both the Agr and TfGr patches. As with the PP soils, relatively high initial levels of inorganic N for Agr and TfGr probably led to higher inorganic N production rates during the soil incubations when compared to non-perennial peanut turfgrass alternatives (OMx, Oga, MulP, and MulC patches) [26]. For all landscape patches except the mulched areas (MulP and MulC), regression analysis revealed a significant linear relationship between nitrification and net mineralization on a whole-core basis (Figure 2). This is not surprising since nitrifying bacteria need ammonia as an energy source thus that nitrification generally increases with increasing ammonia levels in soils [27]. Identifying the underlying mechanism responsible for the lack of this relationship under the mulched landscape areas was beyond the scope of this paper, but factors that may inhibit nitrification include soil C:N ratios above ~22, acid soil pH conditions, and low oxygen availability [15]. We observed that the MulP landscape patch had the highest C:N among all landscape types (~22-23, Table S1), possibly indicating suppressed nitrification and a relatively less active N cycling microbial community in the MulP soils.

Exchangeable Inorganic Soil Nitrogen
Among the non-agricultural soils (all patches except Agr), the PP soils contained the highest median KCl-exchangeable NH 4 + (1.4 mg/kg) but the lowest KCl-exchangeable NO 3 − (0.4 mg/kg) on a whole-core basis ( Figure 3). As discussed above, this relatively low exchangeable NO 3 − pool for the PP soils indicates that N losses via leaching may be taking place. While the use of perennial peanut for urban landscapes has not been studied in terms of its potential for increased N leaching, several studies have looked at this for agricultural settings where perennial peanut is used for forage crops or as a cover crop.
Woodard et al. [29] observed that a forage system with perennial peanut leached more N than a comparable one with bermudagrass. In that study, the authors concluded that perennial peanut might pose threats to groundwater quality under agricultural systems because of its apparent role in subsidizing high NO 3 − levels in the soil.
contained higher mean pools of exchangeable NH4 + and NO3 − than the turfgrass and ornamental patches, though there was considerable spread in the data (Figure 3). It is likely that the mulched landscapes had higher mean exchangeable inorganic N due to the lack of a plant sink to remove inorganic N from the soils [18]. It is also likely that the mulches contained their own pools of N, which leached from the mulch and added to soil N pools [30]. In a study of several urban landscape alternatives, Loper et al. [30] observed that organic soil amendments such as composts could increase inorganic N leaching when compared to soils without amendments. In that study, the authors recommended that landowners did not apply nutrients to mulched areas and that landscape managers recognize that different patches of the same landscape may have different management needs. In general, exchangeable NH4 + was highest in the surface 0-15 cm for all soils, while NO3 − was generally higher with soil depth, perhaps indicating a tendency for NO3 − to move downward in the soil profiles that are predominantly sand (Figure 4). At the 30-52 cm soil depth, exchangeable NO3 − was higher in 4 out of 6 non-agricultural soils than it was in the Agr soil, indicating that the urban landscape patches may pose a greater threat of NO3 − leaching than the agricultural soil ( Figure 4). Turfgrass N fertilization has been found to contribute to the leaching of NO3 − in Florida's sandy soils. For example, Shaddox and Surtain [31] found that applied N in Bermuda grass turf leached between 8% and 12% on a 10% slope. Notably, the NO3 − concentrations in the 30-52 cm depth for the mixed ornamental (OMx) and the gamma grass patch (OGa) were in sharp contrast to each other, with much more NO3 − at depth for the mixed ornamental patch than for the gamma grass patch. Gamma grass is one of the most deeply rooted ornamental grasses, with root depth The mulched landscape patches (MulP and MulC), for which vegetation was absent, contained higher mean pools of exchangeable NH 4 + and NO 3 − than the turfgrass and ornamental patches, though there was considerable spread in the data (Figure 3). It is likely that the mulched landscapes had higher mean exchangeable inorganic N due to the lack of a plant sink to remove inorganic N from the soils [18]. It is also likely that the mulches contained their own pools of N, which leached from the mulch and added to soil N pools [30]. In a study of several urban landscape alternatives, Loper et al. [30] observed that organic soil amendments such as composts could increase inorganic N leaching when compared to soils without amendments. In that study, the authors recommended that landowners did not apply nutrients to mulched areas and that landscape managers recognize that different patches of the same landscape may have different management needs.
In general, exchangeable NH 4 + was highest in the surface 0-15 cm for all soils, while NO 3 − was generally higher with soil depth, perhaps indicating a tendency for NO 3 − to move downward in the soil profiles that are predominantly sand (Figure 4). At the 30-52 cm soil depth, exchangeable NO 3 − was higher in 4 out of 6 non-agricultural soils than it was in the Agr soil, indicating that the urban landscape patches may pose a greater threat of NO 3 − leaching than the agricultural soil ( Figure 4). Turfgrass N fertilization has been found to contribute to the leaching of NO 3 − in Florida's sandy soils. For example, Shaddox and Surtain [31] found that applied N in Bermuda grass turf leached between 8% and 12% on a 10% slope. Notably, the NO 3 − concentrations in the 30-52 cm depth for the mixed ornamental (OMx) and the gamma grass patch (OGa) were in sharp contrast to each other, with much more NO 3 − at depth for the mixed ornamental patch than for the gamma grass patch. Gamma grass is one of the most deeply rooted ornamental grasses, with root depth up to 1.8 m [32], and its deep rooting may be contributing to N uptake deep in the soil profile.
Nitrogen 2022, 3, FOR PEER REVIEW 8 up to 1.8 m [32], and its deep rooting may be contributing to N uptake deep in the soil profile.

Management Implications and Future Research Needs
It is beyond the scope of this paper to make recommendations about which landscape patch is preferable from a N availability or groundwater protection standpoint, as our main intent was to only investigate fine-scale variability in N production in a mixed-vegetation urban landscape. However, some key takeaways are manifest in our results. The first of these is that inorganic N availability and production were, in fact, highly variable among landscape patches at scales of a few meters, in support of our hypothesis. This finding supports the habitat structure framework of urban soil ecology presented by Bryne [19], who argued that the high spatial heterogeneity of human activities in urban landscapes leads to a large range of soil properties at often small scales. The presence of soil amendments such as mulches or plants such as perennial peanuts that can subsidize soil N pools is just two ways that humans influence urban soil properties. We have shown here that inorganic N production is variable in a single urban landscape and have presented some discussion as to why this may be the case for our specific landscape patch types. At a minimum, we argue that urban landscapes should not be broadly managed but that landscape managers should recognize that the nutrient needs of patches within a single landscape may be different and that the nutrient fates in soil under those patches may also be different. This has important implications for how urban soil properties are included in models that aim to predict nutrient transport from urban landscapes. Very likely, we need spatially finer-scale investigations of nutrient fate and transport in urban landscapes, especially those with mixed vegetation or heterogeneous human influences. Too often, urban landscapes are assumed to be covered with turfgrass only, and other possible land covers need to be more fully considered by those who aim to quantify the effects of urbanization on the environment.
A second key takeaway of this work is the implication related to potential N losses by leaching from certain landscape patches. The high nitrification potential of perennial peanut seen here suggests that this turfgrass alternative may produce NO3 − that can be readily leached from sandy soils. However, our sample size was small, and similar work should be conducted in the future to expand the temporal and spatial scope of this work. In particular, we recommend studying N leaching under perennial peanut when it is used as an urban groundcover. We also recommend future work to better understand the mechanisms that drive the differences in potential N losses we observed among landscape patches. Some of the potential drivers include irrigation status, soil pH, moisture content, organic matter content, and variations in the soil microbial community. Finally, because

Management Implications and Future Research Needs
It is beyond the scope of this paper to make recommendations about which landscape patch is preferable from a N availability or groundwater protection standpoint, as our main intent was to only investigate fine-scale variability in N production in a mixedvegetation urban landscape. However, some key takeaways are manifest in our results. The first of these is that inorganic N availability and production were, in fact, highly variable among landscape patches at scales of a few meters, in support of our hypothesis. This finding supports the habitat structure framework of urban soil ecology presented by Bryne [19], who argued that the high spatial heterogeneity of human activities in urban landscapes leads to a large range of soil properties at often small scales. The presence of soil amendments such as mulches or plants such as perennial peanuts that can subsidize soil N pools is just two ways that humans influence urban soil properties. We have shown here that inorganic N production is variable in a single urban landscape and have presented some discussion as to why this may be the case for our specific landscape patch types. At a minimum, we argue that urban landscapes should not be broadly managed but that landscape managers should recognize that the nutrient needs of patches within a single landscape may be different and that the nutrient fates in soil under those patches may also be different. This has important implications for how urban soil properties are included in models that aim to predict nutrient transport from urban landscapes. Very likely, we need spatially finer-scale investigations of nutrient fate and transport in urban landscapes, especially those with mixed vegetation or heterogeneous human influences. Too often, urban landscapes are assumed to be covered with turfgrass only, and other possible land covers need to be more fully considered by those who aim to quantify the effects of urbanization on the environment.
A second key takeaway of this work is the implication related to potential N losses by leaching from certain landscape patches. The high nitrification potential of perennial peanut seen here suggests that this turfgrass alternative may produce NO 3 − that can be readily leached from sandy soils. However, our sample size was small, and similar work should be conducted in the future to expand the temporal and spatial scope of this work. In particular, we recommend studying N leaching under perennial peanut when it is used as an urban groundcover. We also recommend future work to better understand the mechanisms that drive the differences in potential N losses we observed among landscape patches. Some of the potential drivers include irrigation status, soil pH, moisture content, organic matter content, and variations in the soil microbial community. Finally, because urban landscapes are tied to human activities, we recognize that sociocultural variables may drive differences in soil properties as well [33,34]. These sociocultural variables may include the choice of plants that are used in ornamental beds. For example, we observed that the two ornamental patches had very different levels of inorganic N at the greatest soil depth, likely due to greater uptake of N at depth by the deeply rooted gamma grass. This human choice as to which plants to include in a landscape may therefore impact N losses by leaching through the soil profile.
Supplementary Materials: The following are available online at https://www.mdpi.com/article/10 .3390/nitrogen3010009/s1, Table S1, Basic soil physical/chemical properties for landscape patches used in this study; Table S2, Raw data showing nitrification, mineralization, and exchangeable inorganic N for all landscape patches and soil depths.