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DIVISION S-8—NUTRIENT MANAGEMENT & SOIL & PLANT ANALYSIS

Dynamics of Pig Slurry Nitrogen in Soil and Plant as Determined with ¹⁵N

^a Agriculture and Agri-Food Canada, Soils and Crops Research and Development Centre, 2560 Hochelaga Blvd., Sainte-Foy, QC, Canada, G1V 2J3
^b INRA, Unité Sol et Agronomie Rennes-Quimper, 65 Rue de Saint-Brieuc, F35042 Rennes, France
^c Agriculture and Agri-Food Canada, Dairy and Swine Research and Development Centre, P.O. Box 90, 2000, Road 108 East, Lennoxville, QC, Canada, J1M 1Z3

^* Corresponding author (chantignym{at}agr.gc.ca).

	ABSTRACT

TOP ABSTRACT INTRODUCTION MATERIALS AND METHODS RESULTS AND DISCUSSION CONCLUSIONS REFERENCES

 
The fate of pig (Sus scrofa) slurry labeled with ¹⁵N was investigated when applied on a clay soil (fine, mixed, frigid, Typic Humaquept) and a sandy loam (loamy, mixed, frigid, Typic Dystrochrept) cropped to maize (Zea mays L.) in 2000 and to barley (Hordeum vulgare L.) in 2001. The slurry was applied in spring 2000, and plant and soil samples were collected at 6 h (Day 1) and at Days 14, 42, 96, and 413 after application. The samples were analyzed for ¹⁵N content in plant, in whole soil, and in soil NH₄⁺–N, NO₃^––N, organic N, and clay-fixed N pools. Percentage ¹⁵N recovery was >93% in both soils at Day 1 and decreased slowly thereafter. Rapid clay fixation of slurry ¹⁵N occurred at Day 1, and was greater in the clay soil (34% of applied ¹⁵N) than in the sandy loam (11%). At Day 96, less of the applied slurry ¹⁵N was recovered in maize grown on the clay soil (29%), as compared with the sandy loam (50%). At the same period, the residual soil ¹⁵N was mostly present as organic N and NO₃^––N in the sandy loam, and as organic and clay-fixed N in the clay soil. At Day 413, ¹⁵N recovery in barley was about 3% of the initially applied N in both soils. The ¹⁵N recovery was generally higher in the clay soil than in the sandy loam, but total ¹⁵N recovery from the soil–plant system was similar for both soils. We conclude that soil type had little influence on the total ¹⁵N recovery from the soil–plant system, but significantly influenced the fate of slurry N in the various soil pools and plant N uptake on the year of application.

Abbreviations: NDFPS, nitrogen derived from pig slurry

	INTRODUCTION

TOP ABSTRACT INTRODUCTION MATERIALS AND METHODS RESULTS AND DISCUSSION CONCLUSIONS REFERENCES

 
IN THE PROVINCE of Québec, Canada, 9 million m³ of pig slurry are applied each year on agricultural land, representing an input of about 33 million kg N. Mismanagement of this N can increase the risk of pollution of water (Westerman et al., 1985; Spalding and Exner, 1993) and air (Chadwick et al., 1998; Sommer and Hutchings, 2001). At time of spreading, pig slurry generally contains >60% of its N as NH₄⁺ (Sommer and Husted, 1995). This NH₄⁺ can be lost through volatilization, which is generally the major mechanism of slurry N loss (Morvan et al., 1997; Rochette et al., 2001; Sommer and Hutchings, 2001). Under field conditions, 15 to 25% of added slurry NH₄⁺ was found to be immobilized in soil organic matter (Morvan et al., 1997; Sørensen and Amato, 2002). In clay soils, 24% of animal slurry NH₄⁺ was found to be fixed to clay particles (Ross et al., 1985), as compared with 5 to 10% in a sandy loam (Trehan and Wild, 1993). Pig slurry NH₄⁺ is rapidly nitrified in soil after application (Morvan et al., 1997; Chantigny et al., 2001), and can be lost through denitrification and leaching if not taken up by the plants. Nitrogen losses through denitrification in soils amended with pig slurry were found to vary from <1% to >30%, partly depending on soil moisture conditions (Carey et al., 1997; Chadwick et al., 1998; Maag and Vinther, 1999). Nitrogen losses through leaching were detected only at high manure loading rates (Westerman et al., 1985; Spalding and Exner, 1993) and in well-drained soils (Spalding and Exner, 1993).

The apparent N use efficiency of spring-applied pig slurry was estimated to be 10% in maize (Miller and MacKenzie, 1978), 3 to 22% in spring wheat (Garand, 1999), and 30 to 90% in winter wheat (Smith and Chambers, 1992). With ¹⁵N, crop recovery of pig slurry N was found to average 31% in rice (He et al., 1994), 29% in ryegrass (Lolium perenne L.) (Morvan et al., 1997), and 14 to 40% in a barley–ryegrass stand (Sørensen and Amato, 2002).

Even though the general mechanisms of slurry N transformations and losses are known, the actual proportions of pig slurry N that are lost to the environment, recovered by the crop, or left in the soil remain to be elucidated. Moreover, the rate of release of the immobilized and clay-fixed N, and the influence of clay fixation on slurry N availability have been little studied. The proportion of slurry N recovered by the crop as well as the fate and form of slurry N remaining in the soil at harvest would be influenced by soil texture (Sørensen and Amato, 2002).

The use of ¹⁵N as a tracer is the most powerful tool to distinguish the fate of a particular N source from background soil N (Fillery and Recous, 2001). Feeding poultry (Kirchmann, 1990), hog (He et al., 1994; Chantigny et al., 2004) and sheep (Sørensen and Jensen, 1998; Jensen et al., 1999) with a ¹⁵N-enriched diet has been used to obtain animal manure labeled in both its mineral and organic fractions to study the fate of manure N in the soil–plant system. The aim of the present study was to use pig slurry, enriched with ¹⁵N in both its mineral and organic fractions, to determine the fate of slurry N following application on two agricultural soils of contrasting texture.

	MATERIALS AND METHODS

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Manure Characteristics and Experimental Setup
A young (20 kg) castrated pig was fed for 12 d with ¹⁵N-enriched maize and soybean (Glycine max L.) as the protein N sources. Maize and soybean were served in a ratio (2.2:1) typical of commercial feeds used in the province of Québec. Urine and feces were collected as proposed by He et al. (1994) for 20 d after start of ¹⁵N-feeding. Urine and feces collected from Days 4 to 18 were pooled in the same ratio (1.9:1) that they were excreted. A total of 4.5 kg of solids were present in the pooled excreta, and tap water was added to obtain 600 L of a dilute slurry. Diluted slurry was used to ensure uniform field application. The slurry was incubated for 4 wk under anaerobic conditions in a PVC container. Before incubation, 1 L of mature pig slurry was poured into the container to ensure that microorganisms commonly found in standard earthen storage tanks were present. At the time of application, subsamples of the applied slurry were collected and analyzed (Table 1).

After sieving, soil samples were put into plastic bags and immediately brought to the laboratory for analyses. Gravimetric soil water content was measured after soil drying at 105°C for 24 h. Exchangeable NH₄⁺–N and NO₃^––N were extracted by shaking 30 g of field-moist soil with 60 mL of 2 M KCl for 1 h, followed by centrifugation (3000 g, 10 min) and filtration on acid-washed filter papers (Whatman no. 42). This extraction was performed twice on each soil sample and both extracts were pooled (Morvan et al., 1997). After removal of mineral N, the soil residue was resuspended and washed by shaking for 30 min with 100 mL of distilled water. After centrifugation (16000 x g, 10 min), most of the wash water was decanted and the soil was dried at 55°C and finely ground (<100 mesh) with a ball mill.

Ammonium-N content in the KCl extracts was determined by colorimetry (N'konge and Ballance, 1982), whereas NO₃^––N content was measured in the UV at 210 nm with a liquid chromatograph (Model 4000i, Dionex, Sunnyvale, CA) according to Ziadi et al. (1999). The ¹⁵N content of the KCl extracts was determined by steam distillation with MgO (¹⁵NH₄⁺–N) and Devarda (¹⁵NO₃^––N) as described by Keeney and Nelson (1982), but with 0.1 M H₂SO₄ solution instead of H₃BO₃ to trap NH₃. Each distillate was adjusted to pH 4.0 to 5.0 with 0.1 M NaOH, dried at 60°C, and the precipitate was transferred into tin capsules for ¹⁵N determination by mass spectrometry. Stable isotope ratios of N were measured (Stable Isotope Facility Lab, UC Davis, CA) by continuous flow isotope ratio mass spectrometry after sample combustion to N₂ at 1000°C in an on-line elemental analyzer (PDZ Europa, Northwich, Cheshire England).

The total N content of the finely ground whole soil and of the soil residue after KCl extraction was determined by dry combustion (LECO CNS-1000, Leco Corp., St. Joseph, MI). The N content of the soil residue was considered to represent the organic plus clay-fixed fraction of the whole soil N. A subsample of the soil residue was treated with KOBr to quantify clay-fixed N (Silva and Bremner, 1966). The organic N content of the soil was calculated as the difference between total N content in the soil residue and clay-fixed N. The ¹⁵N content of the whole soil and of both the untreated and KOBr-treated soil residues was determined directly on finely ground solid samples by mass spectrometry as described above. All measured soil parameters were expressed on a surface basis (m^–2) with measured soil bulk densities, and the isotopic excess data were used to calculate the ¹⁵N mass balance and distribution among the various soil N pools. For soil samples collected 413 d after slurry application, the total N and ¹⁵N contents were only determined on the whole soil.

Plant samples (0.375 m²) were collected in each microplot 14 and 42 d after slurry application. At 96 and 413 d after application, maize and barley were harvested at maturity (0.75 m²), and grains were separated from the vegetative parts. Plant samples were dried at 60°C until constant weight, and total dry matter yield was calculated. Plant samples were ground to 5 mm. A subsample was then taken and finely ground (< 100 mesh) for total N measurement by dry combustion and ¹⁵N determination by mass spectrometry as described above.

The effects of soil type on the amounts of slurry ¹⁵N that were recovered in the measured soil and plant N pools were tested with a Student's t test (Little and Hills, 1978) at each sampling date.

	RESULTS AND DISCUSSION

TOP ABSTRACT INTRODUCTION MATERIALS AND METHODS RESULTS AND DISCUSSION CONCLUSIONS REFERENCES

 
Slurry Characteristics and ¹⁵N Content
The applied slurry had a low dry matter content (Table 1) close to slurries originating from commercial sow operations in the province of Québec (8–15 kg m^–3). The ¹⁵N content of the slurry mineral N fraction was 1.446 ± 0.036 atom%, compared with 1.458 ± 0.051 atom% for the organic N fraction, indicating a uniform ¹⁵N distribution between the mineral and organic N fractions of the slurry. The distribution of ¹⁵N between the labile and recalcitrant organic N was not investigated. An uneven distribution of ¹⁵N within the organic N fraction could induce some bias when estimating soil N fluxes following slurry application (Sørensen and Jensen, 1998; Jensen et al., 1999). However, since organic N represented only 10% of the slurry total N (Table 1), this uncertainty was considered to be acceptable.

¹⁵N Recovery
The excess ¹⁵N applied as pig slurry was 66.4 mg m^–2 in both soils. Total ¹⁵N recovery 6 h (Day 1) after slurry application averaged 94% in the clay soil and 98% in the sandy loam (Fig. 1) . After 14 d, total ¹⁵N recoveries were 91 and 98% in the clay soil and sandy loam, respectively. Unrecovered ¹⁵N after slurry application has been attributed mostly to ammonia volatilization (Morvan et al., 1997; Sørensen and Amato, 2002). This phenomenon usually occurs during the first few days following slurry application (Morvan et al., 1997; Rochette et al., 2001; Sommer and Hutchings, 2001). Ammonia losses have been reported to account for up to 40% of slurry-added ¹⁵NH₄⁺ on the day of application (Morvan et al., 1997). In our study, the low dry matter content of the slurry, the immediate mixing of pig slurry with surface soil (2- to 3-cm depth), and the frequent rainfall on the days following slurry application (Fig. 2) likely depressed ammonia volatilization, as reflected by the high total ¹⁵N recovery 14 d after application (Fig. 1, Table 3). Even though not statistically significant, the total ¹⁵N recoveries suggest that some volatilization might have occurred in the clay soil, but it was negligible in the sandy loam.

View larger version (28K): [in this window] [in a new window]   Fig. 1. Total 15N recovery in whole soil and aboveground plant parts as a function of time following application of 15N-labeled pig slurry on a clay soil and a sandy loam. Vertical bars represent standard deviation of the mean, n = 4.

View larger version (43K): [in this window] [in a new window]   Fig. 2. Daily precipitation and average air temperature at the site of experiment. Arrows indicate the days of year 2000 when major field operations were performed.

View this table: [in this window] [in a new window]   Table 3. Distribution of pig slurry 15N in various soil and plant N pools as a function of time after application on a clay soil and a sandy loam.

Slurry Nitrogen Distribution and Transformations
The sum of ¹⁵N recovered in the various soil N pools was slightly lower than the ¹⁵N recovery in the whole soil in the sandy loam (<2.4 mg m^–2), and greater differences (4–10 mg m^–2) were found in the clay soil (Table 3). Lack of ¹⁵N recovery in the fractionation procedure could be due to the dissolved organic ¹⁵N in the KCl extracts, which was not accounted for. In addition, greater discrepancies in the clay soil than in the sandy loam could be explained by the loss of colloidal clay particles during the washing of the soil residue with distilled water after KCl extraction. This could have resulted in the loss of some clay-fixed and organic ¹⁵N.

Significant and rapid clay fixation of slurry NH₄⁺ occurred following application. Six hours after application, 34 and 11% of slurry NH₄⁺ were fixed to clay particles in the clay soil and in the sandy loam, respectively (Table 3). Clay fixation of applied NH₄⁺ can last for several weeks, depending on the clay content of the soil (Drury and Beauchamp, 1991). Recently fixed N is gradually released as soil NH₄⁺ is nitrified and removed by the plants (Drury and Beauchamp, 1991; Trehan and Wild, 1993). Our results indicate that in the clay soil, the amounts of clay-fixed slurry N increased from Days 1 to 14 and gradually decreased thereafter (Table 3). By contrast in the sandy loam, the amounts of slurry N fixed to clay markedly decreased from Days 1 to 14 and remained low thereafter. At Day 96, 20% of the added slurry ¹⁵N was still fixed to clay particles in the clay soil as compared with 2% in the sandy loam. The significantly (P < 0.01) greater amounts of clay-fixed ¹⁵N in the clay soil than in the sandy loam (Table 3) would be explained mostly by the greater clay content of the former (Table 2). The proportion of slurry-added N found in the clay-fixed pool of the clay soil at Day 96 is in agreement with Ross et al. (1985), who reported that 24% of total applied N was fixed to clay particles after 6 y of repeated cattle slurry application on a clay soil. Similarly, the proportions of clay-fixed slurry N found in the sandy loam are in line with the values reported (5–10%) by Trehan and Wild (1993) in a laboratory experiment on a similar soil type.

Six hours after application in both soils, slurry ¹⁵N was recovered as NH₄⁺, organic N, and clay-fixed N (Table 3). The amounts of slurry ¹⁵NH₄⁺ recovered in the sandy loam were significantly (P < 0.05) greater and about twice as those in the clay soil. This difference may be explained mostly by the greater clay fixation (34% vs. 11% of slurry-added N) measured in the clay soil than in the sandy loam. In both soils, the amounts of recovered slurry ¹⁵NH₄⁺ markedly decreased from 1 to 14 d after application. For both soils, net rates of soil total NH₄⁺ and ¹⁵NH₄⁺ disappearance were similar (Table 4), indicating that in the present experiment, decreases in soil NH₄⁺ content essentially reflected the dynamics of slurry-derived NH₄⁺. On the contrary, soil NO₃^– accumulated at a rate two to five times higher than ¹⁵NO₃^–, indicating that both slurry- and soil-derived NH₄⁺ were contributing to soil NO₃^– formation. In both soils, the disappearance of ¹⁵NH₄⁺ was compensated by the accumulation of ¹⁵N in the plant, NO₃^––N, and organic N pools (Table 3). From Days 1 to 14, the accumulation of ¹⁵NO₃^– was significantly (P < 0.01) lower in the clay soil than in the sandy loam, possibly reflecting the greater significance of clay-fixation in the clay soil as an alternative pathway for slurry NH₄⁺.

At maize harvest (Day 96), significantly (P < 0.01) less of the applied slurry ¹⁵N was recovered by the crop in the clay soil (29%) than in the sandy loam (50%) (Table 3). This large difference was attributed partly to the greater clay fixation of slurry ¹⁵N measured in the clay soil than in the sandy loam, which likely reduced slurry N availability to maize. Reported plant N use efficiencies for spring-applied pig slurry vary from 3 to 90% in the literature depending on plant species, N loading rate, and management practices (surface-applied vs. incorporated). For a given plant species and N rate, the lowest plant N recoveries were found for surface-applied slurry (Miller and MacKenzie, 1978; Garand, 1999; Sørensen and Amato, 2002), whereas the highest plant N recoveries were found where the slurry was incorporated into the soil (Sørensen and Amato, 2002) or applied to a growing crop (Smith and Chambers, 1992; Morvan et al., 1997). For various crop species, the uptake of pig slurry N generally varied from 30 to 60% where the slurry was applied in the presence of a growing crop (Smith and Chambers, 1992; He et al., 1994; Morvan et al., 1997) and incorporated into the soil (Sørensen and Amato, 2002). Our values for postemergence application of pig slurry to maize are in this range. Barley was grown the year after cropping to maize, and at harvest (Day 413) this crop had recovered 3% of the initially added slurry ¹⁵N in the clay soil, and 4% in the sandy loam (Table 3; Fig. 1). Those values are in line with the 2 to 4% recovery reported by Sørensen and Amato (2002) for a barley crop grown on loamy soils on the second growing season after pig slurry application.

Total maize yields averaged 11.3 and 15.6 Mg ha^–1 in the clay soil and in the sandy loam, respectively (Table 5), and were comparable with values reported in the same area (Tran et al., 1997). In both soils, the proportion of total maize nitrogen derived from pig slurry (NDFPS) varied from 11 to 15% (Table 5). The total N uptake by maize largely exceeded the amount of slurry N applied and could partly explain the high plant ¹⁵N recoveries and low ¹⁵N losses measured during the first growing season. Barley yields in the second year of the experiment were 5.0 and 5.4 Mg ha^–1 in the clay soil and the sandy loam, respectively, and NDFPS was about 2% in both soils. Consequently, plant N uptake was greater in the coarser-textured soil on the year of slurry application, but the residual effect of pig slurry on crop nutrition on the second year was similar for both soils.

Slurry N migrated slowly down the soil profile after application, and at maize harvest (Day 96) most of the soil residual ¹⁵N was still present in the top 10 cm of both soils (Table 6). The clay soil contained significantly (P < 0.05) more residual ¹⁵N than the sandy loam only at the 0- to 10-cm depth. By contrast, significantly (P < 0.05) greater amounts of ¹⁵NO₃^– were present in the sandy loam than in the clay soil at all depths, indicating that the risk of slurry-derived N loss through leaching during the winter period was greater in the sandy loam.

	CONCLUSIONS

TOP ABSTRACT INTRODUCTION MATERIALS AND METHODS RESULTS AND DISCUSSION CONCLUSIONS REFERENCES

	ACKNOWLEDGMENTS

 
This study was financially supported by the Québec Hog Producers Federation (FPPQ) and the Agriculture and Agri-Food Canada Matching Investment Initiative. We gratefully thank Patrice Jolicoeur, Nicole Bissonnette, Johanne Tremblay, and Marie-Anne Langevin for their assistance in various aspects of this study.

Received for publication March 4, 2003.

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TOP ABSTRACT INTRODUCTION MATERIALS AND METHODS RESULTS AND DISCUSSION CONCLUSIONS REFERENCES

 

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