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Article

Soil Dynamics and Nitrogen Absorption by a Natural Grassland under Cow Urine and Dung Patches in an Andisol in Southern Chile

by
Magdalena Ramírez-Sandoval
1,2,*,
Dante Pinochet
2 and
M. Jordana Rivero
3
1
Graduate School, Faculty of Agricultural Sciences, Campus Isla Teja, University Austral of Chile, Valdivia 5090000, Chile
2
Institute of Agricultural Engineering and Soils, Faculty of Agricultural Sciences, Campus Isla Teja, University Austral of Chile, Valdivia 5090000, Chile
3
Rothamsted Research, Sustainable Agriculture Sciences, North Wyke, Okehampton, Devon EX20 2SB, UK
*
Author to whom correspondence should be addressed.
Agronomy 2022, 12(3), 719; https://doi.org/10.3390/agronomy12030719
Submission received: 4 February 2022 / Revised: 7 March 2022 / Accepted: 14 March 2022 / Published: 16 March 2022
(This article belongs to the Special Issue Assessing Sustainability of Ruminant Livestock Forage-Based Systems)
Browse Figures
Versions Notes

Abstract

:
The objective of this study was to assess N dynamics in the soil, and the response in regard to dry matter yield (DM yield; kg·DM·ha−1), N yield (g·N·m−2) and N concentration (g·N·kg−1 DM) under urine patches and dung pats and in the affected zone of the grassland soil over 304 days. The amount of N under the urine and dung patches increased until day 10 and then started to decrease until the end of the experiment, reaching control treatment levels. The DM yield in the urine patch zone and the 0–10 cm zone around the dung pat was higher than in the control treatment throughout the evaluated period, while in the 0–30 cm zone around the urine patch and the 10–20 cm zone around the dung pat the DM yield was negatively affected by the application of excreta. The maximum accumulated N yield was up to two times higher than the control in the 0–10 cm zone of the dung pat, while the mean concentration of N throughout the period was 42% higher than the control for the “urine patch” zone and 47% higher in the 0–10 cm area around the dung pat. The total absorbed N was 19% and 15% for urine and dung excreta, respectively. Further research is needed to explain the variables that might affect the results obtained, and it is necessary to evaluate the botanical composition as a factor that contributes to this effect.

1. Introduction

Excretion from grazing animals, mainly through urine and dung deposition, plays a key role in nutrient recycling in pastoral systems [1], with N being the nutrient that constitutes the largest proportion of these excreta [2,3]. In general, the total N excreted is distributed between dung (20–55%) and urine (45–80%) and the approximate amounts of N supplied via urine and dung patches produced by grazing cows are approximately 500 kg·ha−1 and 1000 kg·ha−1, respectively, assuming patch areas of 0.35 m2 for urine (with 2 L per urination) and 0.07 m2 for dung (with 310 g DM per dung pat), which are typical concentrations of N in urine and dung [3]. Furthermore, the N rate of urine and dung is high enough to cause damage to the leaves and roots of plants where it is deposited [4].
Although the solid fraction of urine is mainly made up of N, potassium, and sulfur, research has focused mainly on N due to its environmental implications. The most important N compound in urine is urea, which makes up more than 70% [5]. According to the type of feeding, when the protein consumption increases, the proportion of N as urea also increases up to 90% in the case of dairy cows [6,7]. The hydrolysis of urea is rapid, and it is hydrolyzed by 80–90% after 48 h of deposition [8]. After the hydrolysis of urea, the nitrification process of NH4+ to NO3− begins [9]. The dynamics of N in grassland after deposition have been extensively studied in temperate climates [2,10,11,12]. Several studies have shown that nitrogen uptake in the area affected by a urine patch ranges from 11 to 49% [2,10,12,13,14,15,16].
Most of the N present in dung is organic and insoluble in water, with approximately 45–65% found in protein and related compounds, 5% in nucleic acids, 3% in ammonia, and the remainder consists of partially degraded nucleic acids, bacterial cell walls, and fiber-bound N [17]. For this reason, the decomposition and mineralization of the N contained in dung can last up to 2 years since much of it is immobilized and accumulates in the soil, whereas the changes in the mineral N of the soil are usually short-lived [11]. Vegetation generally does not penetrate through the dung pat and increases in dry matter around the patch are generally offset by the lost area that is covered by dung [2,10,11,12]. When dung is excreted, it begins to gradually disappear through microbial decomposition of organic matter and through incorporation into the soil by macrofauna [2,18,19,20], although the rate of disappearance can vary widely depending on the climate and moisture content of the stool and according to the presence of specific soil fauna [2]. It has been observed that the patch can take up to 100 days to fully decompose [21,22].
Although there are numerous studies that describe the localized dynamics of N over time in patches of urine and dung, both in the depth of the affected soil and in the absorption dynamics of the plants, there are no studies of this type in Andisols in southern Chile. Most soils in southern Chile are of volcanic origin and are classified as Andisols [23]. They cover between 50–60% of the arable land of the country (5.4 million ha [24]). Due to their andic properties [25,26], these soils have completely different characteristics than other types of soils worldwide. Andisols have been described as soils with variable charge [25], high air- and water-holding capacity [27] and high hydraulic conductivity [28]. In addition, these soils present low bulk density (<0.9 g·cm−3) and elevated levels of organic carbon [29]. For these reasons, the study of the behavior of N from the excreta over time in an Andisol is essential to accurately elucidate the amount of this nutrient that is available for absorption in the grass and the real area or “effective area” of the herbage that is affected by each excreta. The objective of this work was to describe the dynamics of N availability in different layers of the soil profile under urine and dung patches and to determine what part of the N excreted is absorbed by the plants according to the area around the patches that are affected over 10 months.

2. Materials and Methods

2.1. Experimental Site and Design

The experiment was carried out at the “Estación Experimental Agropecuaria Austral” (Austral Agricultural Experimental Station, EEAA), of the “Universidad Austral de Chile” (39°47′ S, 73°14′ W). The mean annual precipitation is 2.472 mm with 75% of it falling from April to September. The ambient temperature is moderate, due to the oceanic influence, with a mean monthly maximum of 15 °C in summer and a minimum of 5 °C in winter [30]. A 30 × 40 m flat area of multispecies grassland was fenced off. The area, which was visually assessed, is composed of several plant species including the predominant Bromus valdivianus (approximately 40%), Trifolium repens (10%), and other plant species (50%), mainly Cychorium intybus, Hypochoeris radicata, and Taraxacum officinale. The experimental area is typically used for research on grazing and behavior evaluations of different forage species. The Bromus valdivianus grassland was established four years before starting this experiment. The meteorological data for the air temperature and daily rainfall were obtained from a meteorological weather station located at the EEAA.
The experimental area was not fertilized or used for grazing for more than 60 days before the beginning of the experiment. Immediately before the application of urine and dung, the herbage was cut to a residue of 5 cm to simulate a typical intensive dairy grazing system in southern Chile.
The experimental design consisted of a complete randomized block with three treatments: urine, dung, and control (no excreta applied). An estimated volume of 2 L of urine (water in the control treatment) was applied in an area of 0.35 m2 from a 1 m height, and 1.8 kg of dung was deposited in 0.07 m2 based on Whitehead [3]. Because the sampling was destructive, the experiment considered a unit of urine patch, dung pat, and a control unit for each date. The sectors of each treatment were placed 1.5 m apart from each other (Figure 1).
Urine was collected from at least seven cows during milking, and fresh dung was collected immediately after deposition when cows were grazing on the same grassland. Both were obtained one day before being applied in the experimental plots. Dung and urine were collected in separate containers and each excreta was mixed and immediately refrigerated at <4 °C until they were applied in the experimental area. The dung mixtures in the container were covered with polyvinyl plastic to prevent contact with air during refrigeration. Dung patches were placed in a plastic semicircle mesh stretched over the 0.07 m2 area in order to avoid sample contamination by the dung.

2.2. Total N Determination in Excretes

The pooled urine sample was immediately cooled to <4 °C to avoid volatilization of ammonia (NH3). On the first day of the experiment, three subsamples of urine were taken to determine the concentration of total N. The dung mixture was refrigerated at <4 °C, and three subsamples were taken to determine the concentration of N. These subsamples were dried and ground to a fine powder (less than 1 mm) to guarantee homogeneity before the analysis of N. Total N was determined through the Kjeldalh digestion method [23]. The total N concentration was 0.685% and 2.73% for urine and dung, respectively, equivalent to 396 and 742 kg·N·ha−1. For the determination of the dry matter, three additional subsamples of the dung mixture were taken, which were then dried in an oven at 105 °C until they reached a constant weight.

2.3. Soil Samples

Soil sampling of the areas affected by excreta began on 4 December 2018 (day 0) and ended on 27 August 2019 (day 267), with a total of 12 samplings, while the sampling of plants took place from 27 December 2018 (day 23) to 8 October 2019 (day 304) with a total of 4 samplings (as defined by Saarijärvi and Virkajärvi [11]). The area was not fertilized during the experimental period of this study. The methodology was based on the works of Saarijärvi and Virkajärvi [11] and Aarons et al. [21].
The first sample was taken 30 min after the application of urine to allow the urine to infiltrate into the soil, corresponding to day 0. The next samples were taken on days 1, 3, 7, 10, 20, 35, 55, 82, 118, 171, and 267. The sampling depths for the urine and control treatments from day 0 to 3 were in the depth layers of 0–5, 5–10, 10–20, 20–30, and 30–40 cm. From day 7, deeper layers (40–50 and 50–60 cm) were also included. In the dung treatment, the dung pat was removed before soil sampling. Soil samples were taken in the area below the plastic mesh. The sampling of the dung treatment began on day 3 with depth layers of 0–5, 5–10, 10–20, and 20–30 cm. From day 7, the 30–40 cm layer was included, and the 40–50 cm layer was included from day 55 (Figure 2). Three subsamples were obtained for each treatment and for each sampling day. Mineral N (NH4+ and NO3−) was determined through the Kjeldalh digestion method [31]. The dung pats were removed, weighed and analyzed for dry matter and total N concentration.

2.4. Herbage Sampling

The herbage was cut at 5 cm in height. The dry matter and N concentration were measured in all treatments on days 23, 49, 199, and 304. In the urine treatment, samples were taken from the center of the ring affected with urine, from the area 0–15 cm and 15–30 cm from the edge of the ring, while herbage samples from dung treatment were taken from the zones 0–10 and 10–20 cm from the edge of the dung pat (Figure 2). To determine the herbage dry matter of the herbage, samples were weighed and then dried in an oven at 40 °C for 4 days. Once dry, the samples were ground to 2 mm in size and the N concentration of each sample was determined according to the methodologies described by Sadzawka et al. [31].

2.5. Statistical Analysis

The experimental design was a randomized complete block design with three treatments (control, dung, and urine). The response variables of each zone analyzed were calculated as the difference for each treatment compared to the control, i.e., changes in DM yield, N content of herbage and N yield caused by dung and urine. The statistical differences between the treatments for each layer and for each day sampled were analyzed by ANOVA. The statistical differences between the control and each zone of urine and dung treatment were analyzed for each day sampled via ANOVA. Horizontal bar graphs were made for each day of soil sampling, presenting the amount of mineralized N for each soil depth layer sampled and for each treatment. GraphPad Prism 5 (GraphPad Software, San Diego, CA, USA) was used for each statistical analysis.

3. Results

3.1. Weather

Air temperature and rainfall recorded during the experimental period are shown in Figure 3. No rainfall occurred during the three first soil samplings, but between one day before day 7 and on day 10, 33 mm of rainfall occurred. In the period from day 20 to day 118, there was almost no rain, except on sampling day 35 when it rained 3 mm. This period corresponded to summer days. For the sampling carried out in the same period (day 0 to 118; 4 December to 1 January 2019) the average temperature was 15.5 °C, with a maximum of 25 °C on 15 February 2019. Before day 171, the rain began to increase, and 12 days before day 171, it rained 36 mm. Ten days before the last sampling, the rainy days were more frequent and abundant, and it rained a total of 67 mm, including the sampling day, which corresponded to the last days of winter and the first days of spring, while the average temperature was 9 °C. From the beginning of the experiment until the first herbage sampling on 27 December 2018, the accumulated rain was 34 mm, mainly in the middle of this period, and on the second herbage sampling day (day 49) the rain was similar, while the average temperature was 16 °C and 15 °C, respectively. Between the second and third herbage samplings, there was 667 mm of rain, and the greatest amount of rain started on day 80 day (1 April 2019), and was equivalent to 91% of the total rainfall in this period, i.e., 26 days before the sampling (6 March 2019), and the average temperature was 10 °C. The accumulated rainfall from the third herbage sampling until day 304 was 909 mm, but a month before the fourth sampling, the rainfall was 10% of the total rainfall in that period, and the average temperature was 9 °C.
The dung pat disappeared in June 2019. If we consider all the zones studied for the urine patch and dung pat (including the area covered by the dung pat), the accumulated DM yield of the control was 60% higher than that of the urine and 38% higher than that of the dung. However, the N yield was higher in the dung zone and lower in the control. The calculated total absorbed N was 75 kg·N·ha−1 from urine and 115 kg·N·ha−1 from dung, which is equal to 19% and 15% of the total N amount deposited, respectively.

3.2. Dynamics of N Mineralization in the Soil

When excreta were applied (day 0) the concentration of N in the soil varied from control only on the upper layer of the urine patch (0–5 cm, p = 0.0231) (Figure 4). One day after urine application, the amounts of N in the soil were 3.5 to 3.9 times higher than the control at all depths at the urine patch. On day 3, the amounts of N in the soil were the greatest at urine patches, ranging from 129 to 196 kg·N·ha−1. On the other hand, intermediate values (65 to 111 kg·N·ha−1) for the soil under the dung pats were observed. The lowest values were observed in the control area (Figure 4). By day 7, N under dung pats and urine patches were similar (overall average 104 kg·N·ha−1). Both treatments had higher N amounts than the control area at all depths. However, by day 10, the soil under urine patches surpassed that under the dung pats regarding N, mainly due to an increase in this variable at the deepest strata (from 20 cm depth and below). No variation in depth for the control area was observed. In general, the N amounts under urine patches and dung pats increased until day 10 and then started to decrease until the end of the experiment. From day 55, there was no difference in soil N at any depth until the end of the experiment (overall average values were 34 and 18 kg·N·ha−1 at day 55 and 267, respectively). The only exception was at day 171 when the area under dung pats in the upper strata (0–10 cm depth) showed a greater value when compared with urine patches and control.

3.3. DM Yield and N Utilization by Herbage

Dry matter yield did not differ from the control under the urine patches throughout the experiment (Table 1). However, lower values than the control on the two rings were observed at day 23 (p < 0.01) in the 15–30 cm zone as well as at day 49 (p < 0.0001), and in the 0–15 cm zone at day 199 (p = 0.0089). Regarding the area affected by the dung pats, the effect was present in the 10–20 cm zone at day 49 (p = 0.0015), in the 0–10 cm zone at day 199 (p = 0.0252), and in the 10–20 cm zone at day 304 (p = 0.0186; Table 1). Likewise, on day 199 the DM yield was higher in the 0–10 cm zone around the dung pats than in the control, whereas on day 304, the DM yield was lower than the control in the 10–20 cm zone.
Nitrogen yield under the urine patches was affected in the early stage of the experiment, specifically in the patch area at days 23 and 49 (p < 0.05), with higher values than the control, and in the outer circle at day 49 (p = 0.0413), with a N yield higher than the control (Table 1). Both the inner and outer circles around the dung pats showed higher values of N yield than the control at days 49 (p = 0.002) and 199 (p < 0.05), respectively, ranging from 130 to 160%.
Nitrogen concentration in the DM was affected by the urine patches, both in the patch area and in the circles at day 23 (p < 0.01), with values between 7 to 2.1 higher than the control (Table 1). At day 49, only the 0–15 cm zone and the patch area were 1.5 and 2 times higher (p < 0.05) than the control, respectively. Regarding the dung pats, the effect was only present at the end of the experiment, when the inner and outer circle showed an N concentration in the DM that was around 40% higher than the control.
The accumulated DM yield throughout the experiment only differed from the control in the outer and inner circles of the urine patches (p < 0.001), showing values between 27% and 44% lower than the control (Table 2). The accumulated N yield showed an opposite trend between the zones. The N yield was around 80% higher than the control in the patch area (p = 0.0002) but was 32% lower in the 15–30 cm zone (p = 0.0074). On the other hand, the N yield was consistently higher in the area affected by the dung pats, and was 1.5 and 2 times greater than the control area for the outer and inner circles, respectively. The concentration of N in the DM was consistently higher than the control in all the areas affected by the excreta (p < 0.05), being on average around one third higher than the control (Table 2).

4. Discussion

4.1. Mineral N Dynamics in the Soil

The focus of our work was to study the application of excreta in summer and under seasonal weather conditions that characterize the region and also to study how the dynamics of nitrogen vary over time.
The mineralization of N from urea began immediately after urine application, which has already been shown by others [8,11], and can be explained by the high proportion of N as CO(NH2)2 (~30–60%) [15], which is rapidly hydrolyzed and made available [2]. On the other hand, although on day 0 there were only statistical differences between the urine and the control in the 0–5 cm layer, the results showed that the amount of mineral N was the highest for the control treatment for the entire experiment. On day 0, the soil had a low moisture level since no rain events had occurred during the previous 10 days. In addition, there were high ambient temperatures. Therefore, these results could be due to the rewetting of the dry soil resulting in a flush of respiration by microbiota [32,33], often increasing within an hour and up to five times higher than in soil constantly kept moist [34,35]. This flush usually persists for up to 10 days after rewetting [36,37,38]. However, the latter did not occur in the control treatment in our experiment. The maximum effect of the urine treatment occurred between day 3 and 10 of the experiment, presumably penetrating to a depth greater than 60 cm. Nevertheless, this mineralized effect began to decline from day 20, reaching values similar to the control from day 35, which was also reported by Saarijärvi and Virkajärvi [11] and Buckthought et al. [39].
Our results showed that there was a rapid mineralization of N under the dung pat between day 3 and 10. After that it quickly fell to control levels until the end of the experiment. In addition, it was estimated that its effect was still present beyond a 40 cm depth in the soil. The fast N mineralization under dung pats was unexpected as the dilution of N in the soil under the dung patch should have been quite slow [40]. Even though there was no rain in that period, it is likely that because the dung presented with an initial percentage of water (90%), there was percolation of the fluids through preferential flows through the macropores that are connected to the soil surface [8,41,42,43]. Additionally, the rapid presence of mineralized N in the soil between days 3 and 10 is contradictory to other studies, which found that the decomposition and mineralization in dung pats may last up to 2 years and the dynamics of excretal N varies greatly depending on climatic and soil conditions [2,10,11,12,44].
However, there is often a rapid increase in the amount of microbial biomass in dung pats during the first 5 days after deposition, and during this period, there is a substantial mineralization of organic N [45]. Moreover, dung decomposition occurs most rapidly in moist conditions [18] and is accelerated by the presence of soil fauna, such as earthworms and dung beetles. The effect of soil fauna in burying and fragmenting dung is reflected in the greater reuse of the nutrients by grassland plants when such fauna is present [46]. In our work, the dung pats had visually disappeared in June 2019, which could be explained by the fact that there is more rainfall in the winter period and its intensity was high, which also contributes to its rate of decomposition [47]. It has been suggested that the proportion of N that was not mineralized was probably immobilized as soil microbial biomass [48], stored as urea and emitted as NH3 [49], as well lixiviated, and with smaller amounts of denitrification in the form of N2O and N2 [14,50,51].

4.2. Dynamics of Mineral N Utilization by Grass

Our results showed that the DM yield in the inner patch area of the urine treatment was not different than the control treatment over time, which is contradictory to several similar studies. Increases in DM yield have been observed even with urine applications equivalent to more than 1000 kg·N·ha−1 [10,11,14,15,39,52]. However, the DM yield in the 0–15 cm and 15–30 cm zones of urine treatment and in the 10–20 cm zone of dung treatment was unusually lower than the control treatment. Even though the botanical composition was not evaluated in this work, it was observed that in the treatments under the addition of N to the soil via both excreta, the proportion of Bromus valdivianus was favored in comparison to the other plants species. However, it has been reported that the effect of urine N on fast-growing species are often visible for about 3 months [53]. Several studies have shown that soil fertility provides the opportunity for fast-growing species to increase in grasslands [54,55,56], and these changes can occur in the short term when a degraded natural grassland is fertilized [57]. Additionally, climatic and others soil variables may exert selection pressure on plant species, which can determine the variability and diversity of genotypes [58,59,60].
According to Balocchi and López [61], naturalized grassland is a multispecies community that is fundamentally dominated by perennial grasses, with a variable proportion of broadleaf species and legumes, which characteristically represent less than 5% of the total annual yield of the grassland. The relative abundance of stress-tolerant broadleaf species such as Hypochaeris radicata are normally associated with soils under low soil fertility [62], which constrains plant growth, root development and can cause plant toxicity, especially for fast-growing species such as Bromus valdivianus [63].
It has been reported that the nutritional quality of a grassland varies according to the diversity of pasture species, which improves as there is a greater presence of better-quality forage species, and fewer species of low nutritional value, such as broadleaf species [64]. The results of our work showed that even though the DM yield was generally lower in the zones around the urine and dung patches, except on day 199 for the 0–10 cm zone of the dung treatment, there was a higher concentration of N (g·N·kg−1 DM) with respect to the control treatment throughout of the entire experimental period. This would imply that in the control treatment, it is possible that there was a greater presence of pasture species of low forage value with a higher fiber density, a characteristic that decreases forage quality [56]. In addition, during the summer, when the high temperatures and summer drought are detrimental to the development of the species, broadleaf species invade the pasture, especially when there are low levels of soil fertility [65]. Thus, the addition of N should have positively affected the pasture species responses.
The amount of N absorbed by the herbage in the “urine patch”, in the 0–15 cm near the urine patch zone and in the total evaluated zone of the dung treatment was greater than the control. Similarly, increases in N uptake and DM yield under higher N rate conditions have been reported [52,66,67,68]. The pasture N uptake has also been found to increase linearly with increasing urine N inputs [52]. Our work showed that the maximum cumulative N yield (g·N·m−2) and N concentration (g·N·kg−1 DM) for both excreta were ~98% and 47% higher than the control, respectively. These values are higher than those reported in other studies, where the absorption of urinary N by pasture was only 25 to 50% compared with the control [10,13,14,69].
Even though the effect of the dung on N mineralization in the soil was only 10 days, the greater absorption of N from the herbage than the control treatment from day 49 in the entire zone evaluated for dung, could be explained due to the slow mineralization of N from organic N of the dung over time, where this nutrient is rapidly absorbed by the herbage [3]. It could also be because the requirements of the pasture may be fulfilled by a high soil mineral N supply because of organic matter mineralization [61,70].
The percentage of N absorption from the urine treatment shown in our experiment is consistent with that reported by other researchers, ranging from 15 to 20% [2,8,11,12,14,71,72,73]. However, the absorption percentage of the dung treatment in our work was higher than that shown in other studies, varying between 0 and 8% [10,11,73].

5. Conclusions

The similar effect of the dung and urine treatments through the depth of the soil and over time would suggest that in the Andisols of southern Chile under natural grasslands, there are many macropores that could induce preferential flows and that could affect nitrogen mobility. However, the effect was short-lived, presumably due to uptake by the pasture and losses due to immobilization by the soil, volatilization, denitrification and leaching However, our results were based on the specific prevailing weather conditions described, thus we consider that it would be relevant to carry out further research that assess the dynamics of nitrogen with the application of excreta at different times throughout the year.
The negative effect outside the urine patch on the DM yield compared to the control treatment with the application of urinary N could be attributed to changes in the botanical composition, and because of pasture species of high forage value with a low fiber content, such as Bromus. However, the application of N from urine and dung would favor the growth of fast-growing species such as Bromus valdivianus, which was observed visually in all the evaluated zones of both excreta. The accumulated absorption of N in the zones affected by urine and dung treatments was up to double that of the control treatment.
This is the first work of this kind carried out in a multispecies natural grassland on volcanic soils in southern Chile, and further research is needed to provide a more detailed explanation of the variables that might influence the effects of applying N from bovine excreta on the pasture characteristics, and to evaluate the botanical composition as an explaining factor.

Author Contributions

Conceptualization, M.R.-S. and D.P.; methodology, M.R.-S. and D.P.; formal analysis, M.R.-S. and M.J.R.; investigation, M.R.-S.; resources, D.P.; data curation, M.R.-S.; writing—original draft preparation, M.R.-S. and M.J.R.; writing—review and editing, D.P. and M.J.R.; visualization, M.R.-S.; supervision, D.P.; project administration, D.P.; funding acquisition, D.P. and M.R.-S. All authors have read and agreed to the published version of the manuscript.

Funding

Agencia Nacional de Investigación y Desarrollo (ANID; Scholarship N° 21160644) funded the doctoral studies. Support in writing up the work was provided by the Biotechnology and Biological Sciences Research Council (BBSRC) through the strategic program Soil to Nutrition (S2N; BBS/E/C/000I0320) at Rothamsted Research.

Data Availability Statement

Data will be made available from the corresponding author upon request.

Acknowledgments

The authors thank Adriana Solis for her support with the laboratory analysis.

Conflicts of Interest

The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.

References

  1. Bardgett, R.D.; Wardle, D.A. Herbivore-mediated linkages between aboveground and belowground communities. Ecology 2003, 84, 2258–2268. [Google Scholar] [CrossRef]
  2. Haynes, R.J.; Williams, P.H. Nutrient cycling y soil fertility in the grazed pasture ecosystem. Adv. Agron. 1993, 49, 119–199. [Google Scholar]
  3. Whitehead, D.C. Nutrient Elements in Grassland: Soil-Plant-Animal Relationships; CABI Publishing: New York, NY, USA, 2000; 384p. [Google Scholar]
  4. Shand, C.A.; Williams, B.L.; Dawson, L.A.; Smith, S.; Young, M.E. Sheep urine affects soil solution nutrient composition and roots: Differences between field and sward box soils and the effects of synthetic and natural sheep urine. Soil Biol. Biochem. 2002, 34, 163–171. [Google Scholar] [CrossRef]
  5. Dijkstra, J.; Oenema, O.; Van Groenigen, J.W.; Spek, J.W.; Van Vuuren, A.M.; Bannink, A. Diet effects on urine composition of cattle y N2O emissions. Animal 2013, 7, 292–302. [Google Scholar] [CrossRef] [Green Version]
  6. Jarvis, S.C.; Scholefield, D.; Pain, B. Nitrogen cycling in grazing systems. In Nitrogen Fertilization in the Environment; Bacon, P.E., Ed.; Marcel Dekker: New York, NY, USA, 1995; pp. 381–419. [Google Scholar]
  7. Petersen, S.O.; Sommera, S.G.; Aaesa, O.; Soegaard, K. Ammonia losses from urine y dung of grazing cattle: Effect of N intake. Atmos. Environ. 1998, 32, 295–300. [Google Scholar] [CrossRef]
  8. Williams, P.H.; Haynes, R.J. Comparison of initial wetting pattern, nutrient concentrations in soil solution and fate of 15N-labelled urine in sheep and cattle urine patch areas of pasture soil. Plant Soil 1994, 162, 49–59. [Google Scholar] [CrossRef]
  9. Haynes, R.J.; Williams, P.H. Changes in soil solution composition y pH in urine affected areas of pasture. J. Soil Sci. 1992, 43, 323–334. [Google Scholar] [CrossRef]
  10. Deenen, P.J.A.G.; Middelkoop, N. Effects of dung y urine in nitrogen uptake y yield of perennial ryegrass. Neth. J. Agric. Res. 1992, 40, 469–482. [Google Scholar] [CrossRef]
  11. Saarijärvi, K.; Virkajärvi, P. Nitrogen dynamics of cattle dung y urine patches on intensively managed boreal pasture. J. Agric. Sci. 2009, 147, 479–491. [Google Scholar] [CrossRef]
  12. Wachendorf, C.; Lampe, C.; Taube, F.; Dittert, K. Nitrous oxide emissions y dynamics of soil nitrogen under 15N-labeled cow urine y dung patches on a sandy grassly soil. J. Soil Sci. Plant Nutr. 2008, 171, 171–180. [Google Scholar] [CrossRef]
  13. Decau, M.L.; Simon, J.C.; Jacquet, A. Fate of urine nitrogen in three soils throughout a grazing season. J. Environ. Qual. 2003, 32, 1405–1413. [Google Scholar] [CrossRef] [PubMed]
  14. Selbie, D.R.; Buckthought, L.E.; Shepherd, M. The Challenge of the Urine Patch for Managing Nitrogen in Grazed Pasture Systems. Adv. Agron. 2015, 129, 229–292. [Google Scholar]
  15. White-Leech, R.; Liu, K.; Sollenberger, L.E.; Woodard, K.R.; Interrante, S.M. Excreta Deposition on Grassland Patches. I. Forage harvested, Nutritive Value and Nitrogen Recovery. Crop Sci. 2013, 53, 688–695. [Google Scholar] [CrossRef]
  16. White-Leech, R.; Liu, K.; Sollenberger, L.E.; Woodard, K.R.; Interrante, S.M. Excreta Deposition on Grassly Patches. II. Spatial Pattern y Duration of Forage Responses. Crop Sci. 2013, 53, 696–703. [Google Scholar] [CrossRef]
  17. Whitehead, D.C. Grassland Nitrogen; CAB International: Wallingford, UK, 1995; 385p. [Google Scholar]
  18. Dickinson, C.H.; Craig, G. Effects of water on the decomposition y release of nutrients from cow pats. New Phytol. 1990, 115, 139–147. [Google Scholar] [CrossRef]
  19. Rowarth, J.S.; Gillingham, A.G.; Tillman, R.W.; Syers, J.K. Release of phosphorus from sheep feces on grazed, hill country pastures. N. Z. J. Agric. Res. 1985, 28, 497–504. [Google Scholar] [CrossRef]
  20. Wilkerson, V.A.; Mertens, D.R.; Casper, D.P. Prediction of excretion of manure y nitrogen by Holstein dairy cattle. J. Dairy Sci. 1997, 80, 3193–3204. [Google Scholar] [CrossRef]
  21. Aarons, S.R.; O’Connor, C.R.; Gourley, C.J.P. Dung decomposition in temperate dairy pastures I. Changes in soil chemical properties. Aust. J. Soil Res. 2004, 42, 107–114. [Google Scholar] [CrossRef] [Green Version]
  22. Lee, C.M.; Wall, R. Cow-dung colonization and decomposition following insect exclusion. Bull. Entomol. 2006, 96, 315–322. [Google Scholar] [CrossRef]
  23. Luzio, W. Suelos de Chile; Departamento de Ingeniería y Suelos, Facultad de Ciencias Agronómicas, Universidad de Chile: Santiago, Chile, 2010; 364p. [Google Scholar]
  24. Besoain, E. Minerales secundarios. In Suelos Volcánicos de Chile; Tosso, J., Ed.; Instituto de Investigaciones Agropecuarias, INIA: Santiago, Chile, 1985; pp. 23–106. [Google Scholar]
  25. Shoji, S.; Nanzyo, M.; Dahlgren, R. Volcanic Ash Soils: Genesis, Properties and Utilization. Developments in Soil Science; Elsevier: Amsterdam, The Netherlands, 1994; 288p. [Google Scholar]
  26. Soil Survey Staff. USDA-Natural Resources Conservation Services, 11th ed.; Natural Resources Conservation Service: Washington, DC, USA, 2010.
  27. Armas-Espinel, S.J.; Hernández-Moreno, J.M.; Muñoz-Carpena, R.; Regalado, C.J. Physical properties of “sorriba”—Cultivated volcanic soils from Tenerife in relation to andic diagnostic parameters. Geoderma 2003, 117, 297–311. [Google Scholar] [CrossRef]
  28. Ellies, A.; Grez, R.; Ramírez, R. La conductividad hidráulica en fase saturada como herramienta para el diagnóstico de la estructura del suelo. Agro Sur 1997, 25, 51–56. [Google Scholar] [CrossRef]
  29. Matus, F.; Amigo, X.; Kristiansen, S. Aluminium stabilization controls organic carbon levels in Chilean volcanic soils. Geoderma 2006, 132, 158–168. [Google Scholar] [CrossRef] [Green Version]
  30. Huber, A. Beitrag ztir Klimatologie und Klimai:ikologie von Chile. Ph.D. Thesis, Ludwig Maximilian Universitat, Mtinchen, Germany, 1975; 81p. [Google Scholar]
  31. Sadzawka, A.; Carrasco, M.; Grez, R.; Mora, M.; Flores, H.; Neaman, A. Métodos de Análisis Recomendados Para los Suelos de Chile; Instituto de Investigaciones Agropecuarias, Serie Actas INIA: Santiago, Chile, 2006; Volume 34, 164p. [Google Scholar]
  32. Fierer, N.; Schimel, J.P. Effects of drying-rewetting frequency on soil carbon and nitrogen transformations. Soil Biol. Biochem. 2002, 34, 777–787. [Google Scholar] [CrossRef]
  33. Miller, A.; Schimel, J.; Meixner, T.; Sickman, J.; Melack, J. Episodic rewetting enhances carbon and nitrogen release from chaparral soils. Soil Biol. Biochem. 2005, 37, 2195–2204. [Google Scholar] [CrossRef]
  34. Rey, A.; Petsikos, C.; Jarvis, P.G.; Grace, J. Effect of temperature and moisture on rates of carbon mineralization in a Mediterranean oak forest soil under controlled and field conditions. Eur. J. Soil Sci. 2005, 56, 589–599. [Google Scholar] [CrossRef]
  35. Rudaz, A.O.; Davidson, E.A.; Firestone, M.K. Sources of nitrous-oxide production following wetting of dry soil. FEMS Microbiol. Ecol. 1991, 8, 117–124. [Google Scholar] [CrossRef] [Green Version]
  36. Fierer, N.; Schimel, J.P. A proposed mechanism for the pulse in carbon dioxide production commonly observed following the rapid rewetting of a dry soil. SSSA 2003, 67, 798–805. [Google Scholar] [CrossRef]
  37. Franzluebbers, A.J.; Haney, R.; Honeycutt, C.; Schomberg, H.H.; Hons, F.M. Flush of carbon dioxide following rewetting of dried soil relates to active organic pools. SSSA 2000, 64, 613–623. [Google Scholar] [CrossRef]
  38. Pesaro, M.; Nicollier, G.; Zeyer, J.; Widmer, F. Impact of drying-rewetting stress on microbial communities and activities and on degradation of two crop protection products. Appl. Environ. Microbiol. 2004, 70, 2577–2587. [Google Scholar] [CrossRef] [Green Version]
  39. Buckthought, L.E.; Clough, T.J.; Cameron, K.C.; Di, H.J.; Shepherd, M.A. Plant N uptake in the periphery of a bovine urine patch: Determining the ‘effective area’. N. Z. J. Agric. Res. 2016, 59, 122–140. [Google Scholar] [CrossRef]
  40. Dickinson, C.H.; Underhay, V.S.H.; Ross, V. Effect of season, soil fauna and water content on the decomposition of cattle dung pats. New Phytol. 1981, 88, 129–141. [Google Scholar] [CrossRef]
  41. Cameron, K.C.; Haynes, R.J. Retention y movement of nitrogen in soils. In Mineral Nitrogen in the Plant-Soil System; Haynes, R.J., Ed.; Academic Press: London, UK, 1986; pp. 166–241. [Google Scholar]
  42. Dörner, J.; Dec, D.; Peng, X.; Horn, R. Effect of land use change on the dynamic behaviour of structural properties of an Andisol in southern Chile under saturated and unsaturated hydraulic conditions. Geoderma 2010, 159, 189–197. [Google Scholar] [CrossRef]
  43. Monaghan, R.M.; Carey, P.A.; Metherell, K.; Singleton, P.L.; Drewry, J.; Addison, B. Depth distribution of simulated urine in a range of soils soon after deposition. N. Z. J. Agric. Res. 1999, 42, 501–511. [Google Scholar] [CrossRef]
  44. Wachendorf, C.; Taube, F.; Wachendorf, M. Nitrogen leaching from N-15 labelled cow urine and dung applied to grassland on a sandy soil. Nutr. Cycl. Agroecosyst. 2005, 73, 89–100. [Google Scholar] [CrossRef]
  45. Yokoyama, K.; Kai, H.; Koga, T.; Kawaguchi, S. Effect of dung beetle, Onthophagus lenzii H. on nitrogen transformation in cow dung and dung balls. Soil Sci. Plant Nutr. 1991, 37, 341–345. [Google Scholar] [CrossRef]
  46. Fincher, G.T.; Menson, W.G.; Burton, G.W. Effects of cattle feces rapidly buried by dung beetles on yield and quality of Coastal Bermudagrass. Agron. J. 1981, 73, 775–779. [Google Scholar] [CrossRef]
  47. Macdiarmid, B.N.; Watkin, B.R. The cattle dung patch. 3. Distribution and rate of decay of dung patches and their influence on grazing behaviour. J. Br. Grassl. Soc. 1972, 27, 48–54. [Google Scholar]
  48. Silva, R.G.; Cameron, K.C.; Di, H.J.; Hendry, T. A lysimeter study of the impact of cow urine, dairy shed effluent, and nitrogen fertiliser on nitrate leaching. Aust. J. Soil Res. 1999, 37, 357–369. [Google Scholar] [CrossRef]
  49. Bussink, D.W.; Oenema, O. Ammonia volatilization from dairy farming systems in temperate areas: A review. Nutr. Cycl. Agroecosyst. 1998, 51, 19–33. [Google Scholar] [CrossRef]
  50. Cárdenas, L.M.; Misselbrook, T.M.; Hodgson, C.; Donovan, N.; Gilhespy, S.; Smith, K.A.; Dhanoa, M.S.; Chadwick, D. Effect of the application of cattle urine with or without the nitrification inhibitor DCD, and dung on greenhouse gas emissions from a UK grassland soil. Agric. Ecosyst. Environ. 2016, 235, 229–241. [Google Scholar] [CrossRef] [Green Version]
  51. Cárdenas, L.M.; Bol, R.; Lewicka-Szczebak, D.; Gregory, A.S.; Matthews, G.P.; Whalley, W.R.; Misselbrook, T.H.; Scholefield, D.; Well, R. Effect of soil saturation on denitrification in a grassland soil. Biogeosciences 2017, 14, 4691–4710. [Google Scholar] [CrossRef] [Green Version]
  52. Di, H.J.; Cameron, K.C. Nitrate leaching losses and pasture yields as affected by different rates of animal urine nitrogen returns and application of a nitrification inhibitor—A lysimeter study. Nutr. Cycl. Agroecosyst. 2007, 79, 281–290. [Google Scholar] [CrossRef]
  53. Richards, I.R.; Wolton, K.M. A note on urine scorch caused by grazing animals. Grass Forage Sci. 1975, 30, 187–188. [Google Scholar] [CrossRef]
  54. Descalzi, C.A.; López, I.F.; Kemp, P.D.; Dörner, J.; Ordóñez, I. Pasture restoration improvement methods for temperate degraded pastures and consequences of the climatic seasonality on soil–pasture complex. J. Agron. Crop Sci. 2020, 206, 130–147. [Google Scholar] [CrossRef]
  55. Dickson, T.L.; Foster, B.L. The relative importance of the species pool, productivity and disturbance in regulating grassland plant species richness: A field experiment. J. Ecol. 2008, 96, 937–946. [Google Scholar] [CrossRef]
  56. Keim, J.P.; López, I.F.; Balocchi, O.A. Sward herbage accumulation and nutritive value as affected by pasture renovation strategy. Grass Forage Sci. 2015, 70, 283–295. [Google Scholar] [CrossRef]
  57. Butkuviene, E.; Butkute, R. Effects of pasture improvement measures on sward productivity, botanical and chemical composition. Zemes Ukio Moksl. 2008, 15, 46–52. [Google Scholar]
  58. Lodge, G. Temperate native Australian grass improvement by selection. N. Z. J. Agric. Res. 1996, 39, 487–497. [Google Scholar] [CrossRef]
  59. Mehrhoff, L.A.; Turkington, R. Microevolution and site-specific outcomes of competition among pasture plants. J. Ecol. 1990, 78, 745–756. [Google Scholar] [CrossRef]
  60. Williams, W. Genetic resources of temperate native and low-input grasses in New Zealand and Australian collections. N. Z. J. Agric. Res. 1996, 39, 513–526. [Google Scholar] [CrossRef] [Green Version]
  61. Balocchi, O.; López, I. Especies pratenses nativas y naturalizadas del sur de Chile [Native and naturalized grassland species of southern Chile]. In Producción Animal; Serie B—20; Latrille, L., Ed.; Facultad de Ciencias Agrarias, Instituto de Producción Animal, Universidad Austral de Chile: Valdivia, Chile, 1996; pp. 65–81. [Google Scholar]
  62. López, I.; Balocchi, O.; Lailhacar, P.; Oyarzún, C. Characterization of the growing sites of six native and naturalized species in the Dominio Húmedo of Chile. Agro Sur 1997, 25, 62–80. [Google Scholar]
  63. Cartes, P.; Mcmanus, M.; Wulff-Zottele, C.; Leung, S.; Gutierrez-Moraga, A.; Mora, M.L. Differential superoxide dismutase expression in ryegrass cultivars in response to short term aluminium stress. Plant Soil 2012, 350, 353–363. [Google Scholar] [CrossRef]
  64. Balocchi, O. Recursos forrajeros utilizados en producción de leche [Forages used in dairy production]. In Competitividad de la Producción Lechera Nacional; Anrique, R., Latrille, L., Balocchi, O., Alomar, D., Moreira, V., Smith, R., Pinochet, D., Vargas, G., Eds.; Universidad Austral de Chile: Valdivia, Chile, 1999; pp. 29–74. [Google Scholar]
  65. Sanderson, M.A.; Skinner, R.H.; Barker, D.J.; Edwards, G.R.; Tracy, B.F.; Wedin, D.A. Plant species diversity and management of temperate forage and grazing land ecosystems. Crop Sci. 2004, 44, 1132–1144. [Google Scholar] [CrossRef]
  66. Di, H.J.; Cameron, K.C. Reducing environmental impacts of agriculture by using a fine particle suspension nitrification inhibitor to decrease nitrate leaching from grazed pastures. Agric. Ecosyst. Environ. 2005, 109, 202–212. [Google Scholar] [CrossRef]
  67. Moir, J.L.; Cameron, K.C.; Di, H.J. Effects of the nitrification inhibitor dicyandiamide on soil mineral N, pasture yield, nutrient uptake and pasture quality in a grazed pasture system. Soil Use Manag. 2007, 23, 111–120. [Google Scholar] [CrossRef]
  68. Moir, J.L.; Malcolm, B.J.; Cameron, K.C.; Di, H.J. The effect of Dicyandiamide on pasture nitrate concentration, yield and N offtake under high N loading in winter and spring. Grass Forage Sci. 2012, 67, 391–402. [Google Scholar] [CrossRef]
  69. Buckthought, L.E.; Clough, T.J.; Cameron, K.C.; Di, H.J.; Shepherd, M.A. Fertiliser and seasonal urine effects on N2O emissions from the urine-fertiliser interface of a grazed pasture. N. Z. J. Agric. Res. 2015, 58, 311–324. [Google Scholar] [CrossRef] [Green Version]
  70. Fontes, J.C.; Cameira, M.R.; Borba, L.G.; Amado, E.D.; Pereira, L.S. Nitrogen dynamics in volcanic soils under permanent pasture. Geoderma 2011, 160, 384–393. [Google Scholar] [CrossRef]
  71. Ledgard, S.F.; Saunders, W.M.H. Effects of nitrogen fertilizer and urine on pasture performance and the influence of soil phosphorus and potassium status. N. Z. J. Agric. Res. 1982, 25, 541–547. [Google Scholar] [CrossRef] [Green Version]
  72. Middelkoop, N.; Deenen, P.J.A.G. The local influence of cattle dung and urine and its interactions with fertilizer nitrogen on herbage dry matter production. In Proceedings of 13th General Meeting of the European Grassland Federation, Banská Bystrica, Czechoslovakia, 25–29 June 1990. Volume II Soil-Grassland-Animal Relationships; Gaborcik, N., Krajovic, V., Zimkova, M., Eds.; European Grassland Federation: Banska Bustrica, Czechoslovakia, 1990; pp. 67–70. [Google Scholar]
  73. Sakadevan, K.; Mackay, A.D.; Hedley, M.J. Influence of sheep excreta on pasture uptake and leaching losses of sulphur, nitrogen and potassium from grazed pastures. Aust. J. Soil Res. 1993, 31, 151–162. [Google Scholar] [CrossRef]
Agronomy 12 00719 g001 550
Figure 1. Schematic design for the experiment of soil samples. Each circle indicates the position of each soil sample for urine, dung and control treatments, and a scheme of the soil sample divided by the depth of each layer.
Figure 1. Schematic design for the experiment of soil samples. Each circle indicates the position of each soil sample for urine, dung and control treatments, and a scheme of the soil sample divided by the depth of each layer.
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Figure 2. A diagram showing the center portion of an experimental unit, the area to which cattle urine and dung were applied, and each zone of grass sampled is shown for both excretes.
Figure 2. A diagram showing the center portion of an experimental unit, the area to which cattle urine and dung were applied, and each zone of grass sampled is shown for both excretes.
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Figure 3. Temperature (°C) and rainfall (mm) for the experimental period. The black arrow indicates the first day of soil sample and gray arrows indicate grass sample dates.
Figure 3. Temperature (°C) and rainfall (mm) for the experimental period. The black arrow indicates the first day of soil sample and gray arrows indicate grass sample dates.
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Figure 4. Amounts (kg·N·ha−1) of nitrogen in the soil under the control (slashed area), urine patches (solid black area) and dung pats (gray area) treatments during the experiment. Horizontal bars represent standard errors of the means. Statistical differences are shown for the comparison between the control, urine and dung within each depth and day. *: p < 0.05; **: p < 0.01; ***: p < 0.001; NS: non-significant.
Figure 4. Amounts (kg·N·ha−1) of nitrogen in the soil under the control (slashed area), urine patches (solid black area) and dung pats (gray area) treatments during the experiment. Horizontal bars represent standard errors of the means. Statistical differences are shown for the comparison between the control, urine and dung within each depth and day. *: p < 0.05; **: p < 0.01; ***: p < 0.001; NS: non-significant.
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Table
Table 1. Grass dry matter (DM) yield (kg·ha−1), nitrogen (N) yield (g·N·m−2) and N concentration (N·g·kg−1 DM) on/around the excretal patches on each sampling date of the experiment (s.e. = standard error of mean). p values for urine and dung are given as differences from the control treatment. Numbers in bold highlight the significant differences (p < 0.05).
Table 1. Grass dry matter (DM) yield (kg·ha−1), nitrogen (N) yield (g·N·m−2) and N concentration (N·g·kg−1 DM) on/around the excretal patches on each sampling date of the experiment (s.e. = standard error of mean). p values for urine and dung are given as differences from the control treatment. Numbers in bold highlight the significant differences (p < 0.05).
Day 23 (27 December 2018)Day 49 (22 January 2019)Day 199 (21 June 2019)Day 304 (8 October 2019)
Means.e.p ValueMean s.e.p ValueMeans.e.p ValueMeans.e.p Value
DM yield (kg·ha−1)
Control1565154 79236 120841 66134
Urine
Patch area+1031570.6491+1451950.4795−157810.1139+1291270.3818
0–5 cm−527540.0090−116670.1595−249660.0089−101500.1691
15–30 cm−968760.0002−40533<0.0001−1811320.2168−1961440.2547
Dung
0–10 cm+3733930.3975+3672100.1151+9163460.0252−1781130.3185
10–20 cm−3421560.1501−239420.0015+3831870.0729−306670.0186
N yield (g·N·m−2)
Control2.20.4 1.00.2 2.20.4 1.40.2
Urine
Patch area+3.20.80.0064+1.30.40.0127+0.80.40.1780+ 0.50.40.2886
0–15 cm+0.70.30.2064+0.30.20.2583+0.40.30.4345−0.30.10.1572
15–30 cm−0.80.20.1203−0.40.10.0413−0.50.20.3592−0.20.40.6419
Dung
0–10 cm+2.31.50.1635+1.30.10.0002+3.61.00.0080−0.30.20.3108
10–20 cm+0.20.20.6137+1.40.20.0002+1.90.80.0463+0.10.30.7800
g·N·kg−1 DM
Control14.82.6 12.62.1 18.23.6 21.11.9
Urine
Patch area+16.82.60.001+12.40.80.0002+9.51.60.0360+2.61.40.3202
0–15 cm+12.81.90.0026+6.51.50.0322+8.21.60.0621−2.00.70.3706
15–30 cm+8.90.40.0067+2.52.30.4410−1.02.10.8202+2.93.90.5378
Dung
0–10 cm+7.03.60.1441+11.24.80.0584+9.02.30.0603+8.31.30.0075
10–20 cm−1.70.50.5531+0.50.50.8108+7.12.60.1370+8.82.30.0416
Table
Table 2. Accumulated grass dry matter (DM) yield (kg·ha−1), nitrogen (N) yield (g·N·m−2) and N concentration (N·g·kg−1 DM) on/around the excretal patches throughout the experiment (s.e. = standard error of mean). p values for urine and dung are given as differences from the control treatment. Numbers in bold highlight the significant differences (p < 0.05).
Table 2. Accumulated grass dry matter (DM) yield (kg·ha−1), nitrogen (N) yield (g·N·m−2) and N concentration (N·g·kg−1 DM) on/around the excretal patches throughout the experiment (s.e. = standard error of mean). p values for urine and dung are given as differences from the control treatment. Numbers in bold highlight the significant differences (p < 0.05).
DM Yield (kg·ha−1)N Yield (g·N·m−2)g·N·kg−1 DM
Mean s.e.p ValueMeans.e.p ValueMeans.e.p Value
Control4232174 6.90.6 67.53.3
Urine
Patch area+1952200.5050+5.60.80.0002+31.83.8<0.0001
0–15 cm−1011840.0004+0.90.20.2079+25.51.1<0.0001
15–30 cm−1757107<0.0001−2.20.20.0074+11.51.70.0125
Dung
0–10 cm+14738140.1071+6.82.10.0096+34.75.50.0003
10–20 cm−5101650.0595+3.70.80.0048+14.03.50.0162
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Ramírez-Sandoval, M.; Pinochet, D.; Rivero, M.J. Soil Dynamics and Nitrogen Absorption by a Natural Grassland under Cow Urine and Dung Patches in an Andisol in Southern Chile. Agronomy 2022, 12, 719. https://doi.org/10.3390/agronomy12030719

AMA Style

Ramírez-Sandoval M, Pinochet D, Rivero MJ. Soil Dynamics and Nitrogen Absorption by a Natural Grassland under Cow Urine and Dung Patches in an Andisol in Southern Chile. Agronomy. 2022; 12(3):719. https://doi.org/10.3390/agronomy12030719

Chicago/Turabian Style

Ramírez-Sandoval, Magdalena, Dante Pinochet, and M. Jordana Rivero. 2022. "Soil Dynamics and Nitrogen Absorption by a Natural Grassland under Cow Urine and Dung Patches in an Andisol in Southern Chile" Agronomy 12, no. 3: 719. https://doi.org/10.3390/agronomy12030719

APA Style

Ramírez-Sandoval, M., Pinochet, D., & Rivero, M. J. (2022). Soil Dynamics and Nitrogen Absorption by a Natural Grassland under Cow Urine and Dung Patches in an Andisol in Southern Chile. Agronomy, 12(3), 719. https://doi.org/10.3390/agronomy12030719

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