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Dep. of Crop and Soil Sci., Michigan St. Univ., 584E PSS Bldg., E. Lansing, MI 48824
* Corresponding author (frankk{at}msu.edu)
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ABSTRACT |
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 TOP ABSTRACT INTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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Abbreviations: LFN, labeled fertilizer nitrogen • N, nitrogen • NO3–N, nitrate-nitrogen
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INTRODUCTION |
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TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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Extensive reviews on the environmental fate of N applications have been conducted by Petrovic (1990) and Walker and Branham (1992). Numerous factors influence N leaching from turfgrass including: N rate and carrier (Geron et al., 1993; Gold and Groffman, 1993; Duff et al., 1997; Morton et al., 1988; Guillard and Kopp, 2004), irrigation rate (Morton et al., 1988), rooting characteristics (Geron et al., 1993; Bowman et al., 1998; Jiang et al., 2000), and N uptake by the turf (Miltner et al., 1996).
Morton et al. (1988) studied three N fertilization rates (0, 97, and 244 kg N ha–1) and two irrigation practices (scheduled by a tensiometer to prevent drainage from the root zone, and an over-watering treatment) on a Kentucky bluegrass and red fescue (Festuca rubra L.) mixture established 4 yr prior. When irrigation was scheduled using a tensiometer, the average NO3–N concentration in leachate for the 0, 97, and 244 kg N ha–1 rates was 0.51, 0.87, and 1.24 mg L–1, respectively. In the overwatering treatments NO3–N concentrations in leachate averaged 0.36, 1.77, and 4.02 mg L–1, for the 0, 97, and 244 kg N ha–1 rates, respectively. The authors concluded that leaching losses from home lawns did not pose a threat to drinking water aquifers.
Gold and Groffman (1993) compared the leaching of NO3–N from four different land uses over a 2-yr period. The four land uses were a home lawn turf (established 6 yr prior), corn (Zea mays L.) grown for silage, a mature mixed oak–pine forest (80–120 yr old), and a septic system. Nitrogen was applied to the turf system at an annual rate of 344 kg N ha–1 divided into five applications. Nitrogen applied to corn was at an annual rate of 202 kg N ha–1. Nitrogen entered the septic system through household wastewater, and the forest system through natural deposition. NO3–N leaching was highest for the septic system, with an average concentration of 59 mg L–1. Leachate concentrations from the silage corn ranged from 3 to 50 mg NO3–N L–1, and leachate from turf ranged from 0.2 to 5.0 mg NO3–N L–1. NO3–N concentration from the mature forest was consistently near 0.2 mg L–1. The authors concluded that septic systems are major contributors of N leaching to groundwater, while the home lawn turf was able to absorb the fertilizer thereby reducing NO3–N leaching.
Starr and DeRoo (1981) applied 15N labeled ammonium nitrate at a rate of 180 kg N ha–1, divided into two applications, to a mixture of Kentucky bluegrass and red fescue. One year after LFN application, 64 and 73% of LFN was recovered within the system when clippings were either removed or returned, respectively. Nitrate-nitrogen concentrations in leachate averaged 1.9 and 2.0 mg L–1 when clippings were either removed or returned, respectively.
Miltner et al. (1996) studied the fate of 15N labeled urea applied to a 1-yr-old Kentucky bluegrass turf. Urea nitrogen was applied at an annual rate of 196 kg N ha–1 divided into five applications over 38-d intervals, defined by either a spring or fall application schedule. Using intact monolith lysimeters (1.2 m deep), NO3–N concentrations in leachate were generally below 1 mg L–1 throughout the study. Only 0.23% of LFN was collected in leachate. The majority of LFN was collected in clippings, thatch, and soil. Total recovery of LFN was 64 and 81% for the spring and fall application schedules, respectively.
Engelsjord et al. (2004) applied ammonium sulfate at 293 kg N ha–1 divided into six applications of 49 kg N ha–1 to Kentucky bluegrass and perennial ryegrass (Lolium perenne L.). Labeled fertilizer nitrogen recovered in Kentucky bluegrass ranged from 77 to 91%, while recovery in perennial ryegrass ranged from 67 to 79%. Small amounts of LFN were found in the 20- to 40-cm soil depth and even though leaching was not directly measured, the authors concluded that leaching was not a significant factor.
Guillard and Kopp (2004) investigated leaching of four different nitrogen carriers in a Kentucky bluegrass turf. Ammonium nitrate, polymer-coated sulfur-coated urea and an organic fertilizer were applied at 147 kg N ha–1 yr–1. Average NO3–N leaching losses were highest for ammonium nitrate with 17% of applied N recovered in the leachate. Leaching losses were primarily during the late fall through early spring time period and the authors concluded that to minimize nitrogen leaching, fertilizers with a higher percentage of slow release nitrogen should be used.
The majority of N fate research has been conducted on relatively young turf stands, ranging in age from 1 to 7 yr; however, the age of a turf stand has been proposed as an important factor in determining the fate of N. Bouldin and Lathwell (1968) suggested that the ability of a soil to store organic N under relatively constant management and climatic conditions, which are typical of turf systems, would decrease with time and eventually an equilibrium level of soil organic N would be obtained. Porter et al. (1980) examined total N content in soil to a depth of 40 cm in 105 turf systems ranging in age from 1 to 125 yr old. The data suggest that soil organic matter accumulation is rapid in the first 10 yr after establishment and slowly builds to an equilibrium at 25 yr, when no further net N immobilization occurs. Porter et al. (1980) concluded that there is a rather limited capacity of the soil to store organic N, and that after 10 yr, the potential for overfertilization is greatly increased.
Petrovic (1990) hypothesized, on the basis of the data of Porter et al. (1980), that older turf sites, or sites with high organic matter contents, should be fertilized at a reduced N rate to minimize the potential for NO3–N leaching. Petrovic (1990) theorized that the rate of N applied to younger turf stands (less than 10 yr of age) should equal the rate at which N is used by the plants, lost to the atmosphere, and stored in the soil. Older turf sites (greater than 25 yr of age) lose the ability to store additional N in the soil, and therefore should be fertilized at a rate equal to the rate N is used by the turf and lost to the atmosphere (Petrovic, 1990).
Duff et al. (1997) examined leaching losses of N applied to a mature Kentucky bluegrass stand. Duff et al. (1997) applied four N fertilization rates, (0, 104, 180, and 257 kg N ha–1) in the form of urea divided into five equal applications. Before this study, the soil had been in turf for at least 25 yr and although soil organic matter contents were not measured, the soil was assumed to have a high organic N content. Suction plate lysimeters, to a depth of 60 cm, were installed in the seventh year of the study to sample leachate from the turf system. Over a 19-mo period (June 1992 through December 1993), NO3–N concentrations in leachate were below 10 mg L–1 for all N fertilization rates, except for two sampling dates in the autumn of the second year for the 257 kg N ha–1 rate. After 8 yr of intensive management, NO3–N concentrations in leachate were not appreciably greater than those reported for younger sites.
Because of the lack of long-term data on nitrogen fate in mature turfgrass stands this research was undertaken. The research objectives were to quantify NO3–N and ammonium-nitrogen (NH4–N) concentrations in leachate and determine the fate of LFN among clippings, verdure, thatch, soil, roots, and leachate for a Kentucky bluegrass turf 10 yr after establishment.
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MATERIALS AND METHODS |
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TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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To construct each lysimeter, a soil monolith was exposed by excavation in increments of approximately 20 cm, and the open-ended stainless steel container was placed over the monolith and downward pressure applied to slide the container over the monolith. Once the containers were completely installed over the monolith core, they were removed from the hole, inverted, and a 3-cm layer of soil was removed from the bottom of the core and replaced with 1- to 2-cm-diam pea gravel. A stainless steel bottom and drain tube were then welded into place and the core reinverted and placed back into the ground atop a manhole structure that provided access to the lysimeter bottom for leachate sampling.
In September 1990, the lysimeters and surrounding area were treated with glyphosate and then sodded with a polystand of Kentucky bluegrass (cv. Adelphi, Nassau, and Nugget). Before the glyphosate [N-(phosphonomethyl)glycine] application, the area had been a turfgrass stand for 6 yr. Between 1991 and 1993, the lysimeters were used for a mass balance N study. From 1994 through 1997, no data was collected from the lysimeters, but the turfgrass was fertilized with urea at an annual rate of 147 kg N ha–1. In 1998, fertilizer treatments were initiated on the lysimeters with two annual N rates of 98 and 245 kg N ha–1. The nitrogen rates are typical of low and high rate fertilization programs for Kentucky bluegrass in Michigan (Rieke and Lyman, 2002). The soil type of the lysimeters and adjacent microplot area was a Marlette fine sandy loam (Fine-loamy, mixed mesic Glossoboric Hapludalfs) with a pH of 7.4. The particle size distributions were 659 g kg–1 sand, 227 g kg–1 silt, and 114 g kg–1 clay.
Turfgrass was mowed twice a week at 7.6 cm with the clippings returned. Irrigation replaced 80% of potential evapotranspiration, estimated by a WS-200 Rainbird Maxi weather station (Rainbird, Glendora, CA).
In the autumn of 2000, 90 microplots were installed in the area adjacent to the lysimeters in a completely randomized design with four replications. Of the 90 microplots, 56 were used for this research, and 34 were reserved for future extractions. The microplots were constructed of 20-cm-diam polyvinyl chloride (PVC) piping 45 cm in length. To preserve the soil structure within the microplots, the leading edge of the PVC piping was beveled and driven into the ground with a hydraulic press until it was flush with the soil surface. Microplots were spaced approximately 31 cm apart.
On 17 Oct. 2000, 15N double-labeled urea (10 atom % excess) was applied in solution to the microplots and lysimeters, followed by 0.5 cm of irrigation. Two of the lysimeters and half of the microplots were treated at a low N rate of 24.5 kg N ha–1, and the remaining lysimeters and microplots were treated at a high N rate of 49 kg N ha–1.
In 2001 and 2002, the lysimeters and microplots received unlabeled N in the form of urea in solution, followed by 0.5 cm of irrigation. The low N treatment was 98 kg N ha–1yr–1, divided into four applications of 24.5 kg N ha–1. The high N treatment was 245 kg N ha–1yr–1, divided into five applications of 49 kg N ha–1. Nitrogen application dates for both treatments were 7 May, 4 June, 3 July, and 8 Oct. 2001 and 8 May, 6 June, 3 July, and 15 Oct. 2002. The high N treatment received additional applications on 13 September, in both 2001 and 2002.
Clipping samples were collected weekly from each microplot throughout the growing season, a subsample collected for analysis and the remainder returned to the microplot. Eight microplots, four from each N treatment, were excavated by carefully digging around the perimeter of the PVC core to ensure the core was not disturbed. Microplots were collected intact on seven sampling dates: 1 Nov., 2000 (15 Days After 15N Treatment); 1 Dec. 2000 (45 DAT); 19 April 2001 (184 DAT); 18 July 2001 (274 DAT); 9 Oct. 2001 (357 DAT); 20 April 2002 (549 DAT); and 17 July 2002 (637 DAT). The PVC pipe containing the microplot was cut away, and the remaining core was partitioned into verdure, thatch, and soil samples, all of which were dried in a convection oven for 72 h at 60°C.
Verdure samples included the crown and leaf portions of the plants. Thatch samples consisted of all plant material above the soil surface after verdure was removed. Soil within the thatch samples was removed by hand massaging, and then ground to a fine powder with a mortar and pestle. Thatch soil was analyzed as a soil depth. Clipping, verdure, and thatch samples were weighed and then ground to pass a 0.5-mm screen with an UdyMill Cyclone Sample Mill (Udy Corporation, Fort Collins, CO).
Soil was partitioned into depths of 0 to 5, 5 to 10, 10 to 20, and 20 to 40 cm. At each soil depth, two subsamples were taken. The first subsample (250 g oven dry weight) was placed in a 500-mL fleaker (Corning Glass Works, Corning, NY) with approximately 10 mL of a 5% (w/v) sodium hexametaphosphate dispersion agent and filled with water to reach a 450-mL volume. The fleaker was capped and placed on a horizontal shaker for 24 h to displace the soil from the roots. The fleaker cap was removed and the fleaker was placed on a US Standard Sieve (0.05 mm) under running water, to float the roots and fine soil particles out of the fleaker with the water, leaving the heavier soil particles in the fleaker. The smaller soil particles passed through the sieve, while the roots were retained. Root samples were collected and dried at 60°C in a convection oven for 72 h, weighed, and then ground to pass a 0.5 mm screen with a UdyMill Cyclone Sample Mill. The second subsample, 320 cm3 in volume, was ground to a fine powder with a mortar and pestle after all visible root material was removed. The ground samples of clippings, verdure, thatch, roots, and soil were dried for an additional 24 h in a convection oven at 60°C.
Leachate collected from the monolith lysimeters was collected continuously throughout the experiment. Data for leachate will be reported through the last microplot sampling date on 17 July 2002. The volume of leachate was measured when the jugs were approximately 75% full, and two subsamples were taken. One subsample was sent to the Soil and Plant Nutrient Testing Lab, Michigan State University, to determine NO3–N and NH4–N concentrations by flow injection analysis (QuikChem 10–107–04–1-A) with a LaChat rapid flow injection unit (LaChat Instruments, Milwaukee, WI). The second subsample was used to determine 15N enrichment by the N diffusion technique of Moran et al. (2002). Because of the low 15N concentration in the leachate, analysis was performed for NO3–N and NH4–N species combined.
Total N concentration and 15N enrichment in clipping, verdure, thatch, root, soil, and leachate samples were determined with a Europa 20–20 mass spectrometer (Europa Scientific, Crewe UK). Mass of N and percentage of 15N recovered calculations were from Kessavalou (1994).
The experimental design was a completely randomized design. NH4–N and NO3–N concentration, LFN recovered, and the percentage of applied LFN recovered (%LFN) were determined for each leachate sampling date. Leachate data were analyzed as a two-factor experiment, with N rate and sampling date as factors. Soil and root LFN and %LFN data were analyzed as a three-factor experiment with N rate, DAT, and depth as factors. Potential correlation between the measurements taken on the same core at different depths was accounted for by analyzing the measurements taken at different depths as repeated measures. All depths for the soil and root samples were then totaled to determine the cumulative amount of LFN and the %LFN at each sampling date. Weekly clipping data was summed to determine the cumulative amount of LFN and %LFN from all weekly sampling dates before the corresponding microplot sampling date. Leachate data was summed to determine the cumulative amount of LFN and %LFN from all sampling dates before the corresponding microplot sampling date. Kentucky bluegrass clipping, verdure, thatch, soil, root, and leachate components were combined to determine the total amount of LFN and the %LFN at each sampling date. The clipping, verdure, thatch, soil, root, leachate, and total recovery data were analyzed as a two-factor experiment with N rate and DAT as factors. Treatment differences were analyzed by the Proc Mixed procedure of SAS (SAS Institute Inc., 2001). When appropriate, means were separated using Fischer's LSD procedure at the 0.05 probability level.
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RESULTS AND DISCUSSION |
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TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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Nitrogen in Clippings
Total clipping yield and total N recovered in clippings was significantly different between the two N rates. For the low and high N rate treatments clipping yield was 2091 and 3531 kg ha–1, respectively. Total N recovered in clippings from 4 May 2001 to 12 July 2002 was 73 and 134 kg N ha–1 for the low and high N rate treatments, respectively. Percentage nitrogen in the clippings averaged 3.5 and 3.8% for the low and high N rate treatments, respectively. The total amount of LFN recovered in clippings was 1.7 and 4.8 kg N ha–1 for the low and high N rate treatments, respectively (Table 1, Fig. 1). The Kentucky bluegrass treated at the high N rate had a higher amount of LFN in clippings than the low N rate on all sampling dates. The percentage of applied LFN recovered in clippings was 7 and 9.7% for the low and high N rate treatments, respectively. Kentucky bluegrass treated at the high N rate had a greater percentage of applied LFN recovered than the low N rate on all sampling dates.
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The amount of LFN recovered in verdure was similar to the values reported by Miltner et al. (1996) and greater than the values reported by Frank (2000), for similar N rates applied to Kentucky bluegrass turf. Miltner et al. (1996) reported the percentage of applied LFN recovered in verdure declined from 23% at 199 DAT to 0.7% at 752 DAT for a fall application of 39.2 kg N ha–1. These values were similar to the decline from 21% at 184 DAT to 1.0% at 637 DAT for our research.
Nitrogen in Thatch
At the high N rate, the amount of LFN recovered was greater than at the low N rate for all sampling dates, except at 637 DAT when there was no difference (Table 1). The amount of LFN in thatch, regardless of N rate, declined after the 184 DAT sampling date. Within each N rate the highest amount of LFN was at 184 DAT, for the low and high N rate, 4.6 and 6.8 kg N ha–1, respectively. At 274 DAT for the low and high N rates, the amount of LFN declined to 1.1 and 1.9 kg N ha–1, respectively. From 184 DAT to 274 DAT, the percentage of applied LFN recovered declined 14 and 10% for the low and high N rates, respectively.
Nitrogen in Roots
There was a N rate x DAT x depth interaction for the amount of LFN recovered in roots. The 0–5 cm depth, regardless of N rate, contained a higher amount of LFN in roots than the 5–10, 10–20, and 20–40 cm depths (data not presented). This was expected because the 0–5 cm depth had the highest mass of roots. The 0–5 cm depth, regardless of N rate, averaged 13c451 kg roots ha–1. The 5–10, 10–20, and 20–40 cm depths combined, regardless of N rate, averaged 2910 kg roots ha–1. Although differences were observed between the 5–10, 10–20, and 20–40 cm depths, the amount of LFN recovered at these depths was typically less than 0.2 kg N ha–1. Therefore, the amount of LFN recovered for all depths was summed and statistical analysis performed on the total LFN recovery in roots.
There was a N rate x DAT interaction for the amount of LFN recovered in roots. The high N rate had a higher amount of LFN recovered in roots than the low N rate on 2 of 5 sampling dates (Table 1). At 184 DAT, the amount of LFN recovered for the low and high N rates was 3.7 and 5.1 kg N ha–1, respectively. By 637 DAT, the amount of LFN in roots declined to 1.5 and 2.0 kg N ha–1 for the low and high N rates, respectively. From 184 to 637 DAT, there was a decrease of 9 and 13% of applied LFN recovered for the low and high N rates, respectively.
Kentucky bluegrass at the high N rate had a higher percentage of applied LFN recovered in roots than the low N rate on 3 of 5 sampling dates. Regardless of N rate, the percentage of applied LFN recovered declined from 184 DAT to 637 DAT. At the low N rate, the percentage of applied LFN recovered decreased from 15% at 184 DAT to 6% at 637 DAT. At the high N rate, the percentage of applied LFN recovered decreased from 21% to 8% from 184 to 637 DAT, respectively. These results were similar to the values reported by Power and Legg (1984), who reported that the percentage of applied LFN recovered in roots in a crested wheatgrass [Agropyron desertorum (Fisch. Ex Link) Schult.] grassland decreased from 15 to 5% from 1 to 3 yr after application, respectively. The authors concluded that some of the applied LFN initially immobilized in the roots was mineralized and would account for a portion of the cumulative increase of 15N recovered in the "tops" of the plant.
Nitrogen in Soil
There was a N rate x DAT x depth interaction for the amount of LFN recovered in soil. The 0–5 cm depth, regardless of N rate, had the highest amount of LFN (data not presented). The remaining depths, regardless of N rate, revealed no trends. The total amount of LFN in soil fluctuated among sampling depths and dates. Miltner et al. (1996) and Frank (2000) noted similar fluctuations and attributed them to mixing procedures and sample variability.
When the amount of LFN recovered from all soil depths was summed and analyzed, there was a significant N rate x DAT interaction. The high N rate had a higher amount of LFN recovered than the low N rate for all sampling dates, except at 274 DAT where there was no difference (Table 1). The highest amount of LFN recovered was 26.6 kg N ha–1 at 15 DAT for the high N rate.
The amount of LFN recovered was similar to the values reported by Frank (2000) and greater than the values reported by Miltner et al. (1996). Miltner et al. (1996) reported average percentage recovery of applied LFN of 16% for a fall application of 39.2 kg N ha–1. This value was smaller than the 51 and 38% averages for our research at the low and high N rate, respectively. Frank (2000) reported average percentage recovery of applied LFN in soil of 45 and 30% for applications of 24.4 and 48.8 kg N ha–1, respectively.
Nitrogen in Leachate
LFN
The cumulative amount of LFN recovered in leachate is presented in Fig. 2. The amount of LFN in leachate for the low N rate ranged from 0 to 0.08 kg N ha–1. The amount of LFN in leachate for the high N rate ranged from 0.01 to 0.73 kg N ha–1.
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On the same site as our research, from 1991 through 1993, Miltner et al. (1996) applied N as urea at 39.2 kg N ha–1 defined by either a spring or fall application schedule. Miltner et al. (1996) reported 0.2% of applied LFN recovered in leachate from a fall application. For our research, leachate from the low N rate had a similarly low amount of LFN. However, leachate from the high N rate had drastically different results than the Miltner et al. (1996) research. Over the 2 yr of our research, 11% of applied LFN was recovered in leachate for the high N rate (49 kg N ha–1 rate).
NH4–N and NO3–N Concentration
NH4–N concentrations were typically below 0.07 mg NH4–N L–1, regardless of N rate. Flow-weighted means for the low and high N rates were 0.04 and 0.13 mg NH4–N L–1, respectively. These values were similar to flow-weighted means averaging 0.13 mg L–1 reported by Miltner et al. (1996). Brown et al. (1982) reported that NH4–N losses contributed very little of total N losses from putting greens and only occasionally exceeded 1 mg L–1.
There was a N rate x sampling date interaction for the concentration of NO3–N recovered in leachate. The high N rate had a higher concentration of NO3–N in leachate than the low N rate on 31 of 36 sampling dates when leachate was collected from both the low and high N rate treatments (Fig. 3). The NO3–N concentration for the low N rate was less than 5 mg L–1 on 26 of 36 sampling dates. The flow-weighted mean for the low N rate was 4 mg NO3–N L–1. Nitrate-nitrogen concentrations in leachate for the high N rate were greater than 20 mg L–1 on 20 sampling dates. On eight sampling dates, the NO3–N concentration ranged between 30 and 40 mg L–1. The flow-weighted mean for the high N rate was 21 mg NO3–N L–1.
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Mass Balance
Kentucky bluegrass treated at the high N rate had a higher amount of LFN than the low N rate on all sampling dates (Table 1). The highest amount of LFN recovered value was 39.7 kg N ha–1 at 15 DAT for the high N rate. Soil accounted for the highest amount of LFN among the turfgrass, soil, and leachate components, regardless of N rate or sampling date.
The average percentage recovery of applied LFN was 78 and 73% for the low and high N rates, respectively. The highest recovery was 96% at 357 DAT for the low N rate. The average total percentage recovery of applied LFN for our research agrees with previously reported recovery values (Starr and DeRoo, 1981; Miltner et al., 1996; Frank, 2000; Engelsjord et al., 2004). Total percentage recovery of applied LFN for these studies ranged from 64 to 91%. These researchers suggested that denitrification and NH3 volatilization losses were responsible for incomplete recovery of applied 15N. Substantial losses of N can occur through denitrification when conditions are appropriate. Horgan et al. (2002) compared denitrification losses from bare soil and Kentucky bluegrass. Denitrification losses (N2 and N2O) accounted for 7 and 19% of applied LFN for bare soil and Kentucky bluegrass systems, respectively. Mancino et al. (1988) reported little to no denitrification losses when the soil was below 80% saturation in combination with low soil temperatures, however, when saturated soil conditions were combined with high soil temperatures denitrification losses were high. Our research returned 80% evapotranspiration twice a week, which at least temporarily may have created favorable conditions for denitrification losses.
Volatilization losses may also have accounted for incomplete recovery of applied 15N. Nelson et al. (1980) reported 5 and 39% of applied N volatilized from Kentucky bluegrass following urea applications when a thatch layer was absent or present, respectively. Torello et al. (1983) reported that approximately three times as much N was lost from Kentucky bluegrass following an application of solubilized urea as compared with a prilled urea application.
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CONCLUSIONS |
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TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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The amount of LFN recovered in leachate from lysimeters treated at the high N rate was higher than anticipated. From 17 Oct. 2000 through 17 July 2002, a period of 637 d, 1 and 11% of applied LFN was recovered in leachate for the low and high N rates, respectively. Flow-weighted means for the low and high N rates were 4 and 21 mg NO3–N L–1, respectively. The results for the low N rate were similar to the results reported by Miltner et al. (1996) at the same site from 1991–1993, and indicate that at the low N rate the potential for groundwater contamination is minimal. At the high N rate, the amount of LFN recovered and the concentration of NO3–N in leachate were substantially greater than the values reported by Miltner et al. (1996). At the high N rate, the NO3–N concentration in leachate was typically two or more times greater than the EPA safe drinking water standard of 10 mg NO3–N L–1. This research indicates that single dose, high rate, water soluble N applications (49 kg N ha–1 application–1) to mature turfgrass stands should be avoided to minimize the potential for NO3–N leaching. However, just as the original research on this site was conducted over a relatively short time frame of 2 yr, the results presented in this paper were from 2 yr of data collection, albeit from a 10-yr-old continuously fertilized turf stand. The long-term N fate research at Michigan State Univ. is ongoing and future results will be reported. This article should be considered as the first in a series of consecutive research reports that will be published from the MSU long-term N fate research area. Although this research clearly indicates a cause for concern with respect to high rate, water soluble, nitrogen applications causing elevated levels of NO3-N leaching from mature turfgrass stands, subsequent years of data from this site should be considered before drawing definitive conclusions.
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ACKNOWLEDGMENTS |
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Received for publication April 28, 2005.
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REFERENCES |
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TOPABSTRACTINTRODUCTIONMATERIALS AND METHODSRESULTS AND DISCUSSIONCONCLUSIONSREFERENCES |
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