On-line version ISSN 0718-9516
J. Soil Sci. Plant Nutr. vol.12 no.1 Temuco 2012
Journal of Soil Science and Plant Nutrition, 2012, 12 (1), 153-163
Effect of liquid cow manure amendment on dimethenamid persistence in a volcanic soil
O. Candia1,2, M. de la Luz Mora1,2, R. Demanet1,3, G. Briceño1,2, G. Palma1,2*
1Center of Plant, Soil Interaction and Natural Resources Biotechnology, Scientific and Technological Bioresource Nucleus, Universidad de La Frontera, Avenida Francisco Salazar 01145, Casilla 54-D, Temuco, Chile.'Corresponding author: email@example.com
2Departamento de Ciencias Químicas y Recursos Naturales, Universidad de La Frontera, Casilla 54-D, Temuco, Chile.
3Departamento de Producción Agropecuaria, Universidad de La Frontera, Casilla 54-D, Temuco, Chile.
The effect of liquid cow manure (LCM) on dimethenamid persistence was studied using amended soils with various stabilization times and LCM doses corresponding to specific field applications. Soils were amended with LCM doses equivalent to 100,000, 200,000, and 300,000 L ha-1. Dimethenamid (2-chloro-N-(2, 4-dimethyl-3-thienyl]-N-[2-
Keywords: dimethenamid, liquid cow manure, Andisol, microbial respiration, persistence.
The growing demand for products of animal origin has resulted in a higher dairy plant production of slurry or liquid cow manure (LCM), which consists of excrement, urine, and washing water. LCM is generally stored in uncovered pits and is spread on pastures or soils that are subsequently used to sow maize for animal feed.
The application of LCM to agricultural soil is considered effective waste management option because of nutrient recycling and the presence of organic matter (OM), which improves nutrient content, microbial bio-mass, and soil enzyme activity (Perucci et al., 2000; Dungan et al, 2003; Said-Pullicino et al, 2004). Various authors have reported on the effects of animal manure on the dissipation of herbicides (Sluszny et al., 1999; Moorman et al., 2001; Farenhorst et al., 2006; Briceño et al, 2007). An increase in biological activity resulting from a high amount of both stable soil organic matter and dissolved organic matter could have various effects on degradation, adsorption, and leaching herbicide processes (Topp et al, 1996; Perrin-Ganier et al, 2001; Albarrán et al, 2004).
In Southern Chile, LCM is applied to soils prior to planting the maize fodder crop (Salazar et al., 2003; Briceño et al., 2010) between August and October; however, the LCM that is applied is highly variable, containing up to 300,000 Lha-1. Moreover, the amount of time required between the most current application of LCM and herbicide application is unknown. This practice may be responsible for the decrease in weed control that has been observed in some fields (Briceño et al. 2008; Aguilera et al, 2009). The evaluation of microbial respiration and FDA activity has been useful for evaluating the response of freshly amended soils after the application of pesticides (Perucci et al., 2000; Dungan et al., 2003).
The objective of this study was to determine the effects of the LCM dose and stabilization time of amended soils on dimethenamid degradation under controlled conditions in a volcanic soil. This research will contribute to specific development strategies within agricultural practices that aim to streamline LCM and herbicide use and minimize environmental impacts.
2. Materials and methods
The laboratory experiment was conducted in 2010. The soil used in this study was an Andisol with a sandy loam texture from Southern Chile, termed the Vilcun series (Pachic Melanudands), from the town of General Lopez (38Â° 41' LS, 72Â° 21' LW, 200 m.a.s.l.). The annual rainfall is approximately 2,000 mm per year, and the average temperature is 15Â°C. The soil was collected from a superficial layer to a depth of 20 cm and sieved through a 2-mm mesh. It contained no prior application of LCM or dimethenamid. The LCM was obtained from an open slurry pit located near the dairy plant.
Dimethenamid (99% purity) was supplied by Sigma-Aldrich Chemical Company, St Louis, MO. In the laboratory, 1.2 mg kg-1 dimethenamid was used, with the assumption that the herbicide is distributed at a depth of 20 cm and that the soil density is 0.75 g mL-1. This dose correlates to a field application of 1.5 kg ha-1.
2.1. Chemical analysis of LCM and soils
The LCM analysis was performed according to the methodology of Peters et al. (2003) and with previous information from our research group (Briceño et al., 2008). Briefly, the pH and electrical conductivity (EC) were measured in non-diluted LCM. To estimate the dissolved organic carbon (DOC), the LCM was centrifuged and the supernatant was filtered, lyophilized, and analysed as a total organic carbon (EURO EA 3000 Elemental Analyzer). Dry matter (DM) was determined through water evaporation of the LCM at 70 Â°C. Next, the OM content was estimated by finding the mass difference between the LCM and ash mass. Several chemical LCM characteristics were identified: DM 53.0 g L-1, EC 5.9 dS m-1, OM 71.1 mg kg-1, DOC 2140 mg L-1, pH 7.5, and N 28.6 g kg-1. Soil samples were characterized from Briceño et al. (2008) based on methods described by Sadzawka et al. (2006) and are included in Table 1.
2.2. Preparation of LCM-amended soils
LCM was applied to soil in doses of 0, 70, 140, and 200 mL kg-1, which are equivalent to field doses corresponding to 0, (D0), 100,000 (D100), 200,000 (D200) and 300,000 (D300) L ha-1, respectively. The moisture of the non-amended and amended soils was adjusted to 70% of the field capacity and was also adjusted periodically by adding distilled water. Four kilograms of LCM-amended and non-amended soils were pre-in-cubated in the absence of light at 20Â°C without herbicide application in open polypropylene bags for each pre-incubation time (1, 10, 20, 30 and 60 days). For the CO2 evolution and FDA study, 500 g of each pre-incubated soil was spiked with 12 ml of 50 mgL-1 of dimethenamid aqueous solution and then thoroughly mixed. In the degradation study, a fraction of 1.5 kg of each pre-incubated soil was contaminated with 36 mL of the same dimethenamid solution. The dimethenamid dose corresponded to 1.2 mg kg-1, which was equivalent to the field dose. The studies were conducted three times, and values were measured with respect to the reference soil, which did not contain any herbicide application.
After the corresponding pre-incubation time, the soil samples were chemically characterized (Table 1) according to Sadzawka et al. (2006).
2.3.Â Microbial respiration assay
The respiration study was based on a method described by Alef (1995). Sub-samples consisting of 50 g of each soil were placed inside a 1 L sealed flask containing a vial with distilled water and a second vial with 10 mL of NaOH 0.5 M to capture the CO2 released from the soil. The experiment was performed at 20Â°C in the absence of light. The vials containing the NaOH solution were sampled and replaced periodically for 60 days. The CO2 in the vials was determined with 0.5 M HCl using titration. The data were expressed as C-CO2 μg g-1 soil.
2.4.Â FDA assay
The FDA hydrolytic activity assay was performed by measuring the release of fluorescein as described by Adam and Duncan (2001). One gram of each soil was incubated in a 50 mL conical tube containing 7.5 mL of 0.06 M potassium phosphate buffer (pH 7.2). The reaction was initiated by adding 0.1 mL of 1 mg mL-1 FDA solution, and then the solution was incubated at 30Â°C and shaken at 100 rpm for 20 min. At this time, the reaction was stopped by adding 7.5 mL of chloro-form/methanol (2:1 v/v). The samples were then centrifuged for 10 min, and the absorbance was measured at 490 nm. The FDA activity was measured for 60 days after the dimethenamid application. The fluores-cein concentration was calculated using a calibration curve generated with known FDA concentrations, and the data were expressed as FDA μg g-1.
2.5.Â Dimethenamid degradation assay
In the degradation study, a fraction of 50 g of each soil was taken for 60 days after the dimethenamid treatment. The samples were stored at -20Â°C until the herbicide was extracted. The residual dimethenamid was determined for the HPLC analysis, and the herbicide concentration matched first-order kinetics (Nkedi-Kizza and Brown, 1998).
2.6.Â Residual dimethenamid analysis
Dimethenamid was extracted using a modified method proposed by Anderson et al. (2005). Ten grams of each soil sample was extracted with 10 mL of a mixture of methanol/water (95/5 v/v) and was then shaken at 200 rpm for 1 h at 20Â°C, followed by 30 min in an ultrasonic bath. The supernatant was collected, and this procedure was repeated three times. The combined supernatant extracts were centrifuged for 10 min and filtered through 0.45-Â¡im membranes (Millipore). The liquid extract was concentrated at 5 mL at 40Â°C in a rotary evaporator (Heidolph WV 2000). These extracts were then liquid-liquid extracted with 10 mL of hexane in a separating funnel, and this process was repeated 3 times. The hexane extract was dried in a rotary evaporator, and the sample was dissolved in 2 mL of methanol. The solution was filtered through a 0.22-μm filter, and the residual herbicide was measured by HPLC, based on a method established by Crawford et al. (2002). The analysis was performed in HPLC (Merck Hitachi, model 3400) equipped with a UV detector at 210 nm on a Symmetry C18 column (Waters, 5 μm, 250 mm x 4.6 mm). The mobile phase used acetonitrile/water (55- 45%) at a flow rate of 1 mL min-1, and the injection volume was 20 μL.
2.7.Â Data analysis
The data were subjected to statistical analyses of variance (ANOVA), and all mean separations were determined using the Tukey test (p ≤ 0.05).
3. Results and discussion
3.1. Biological assessments
Figure 1 shows that the LCM amendment had substantially increased the CO2 during the first day of incubation for soils that had been pre-incubated for one day. An increase in CO2 did not occur for other pre-incubation times that had the same impact; however, significant increases were observed in the initial production of CO2. During the first day of pre-incubation, the CO2 production was greater than 47 μg C-CO2 g-1 d-1 in D0, and it increased 62, 128, and 232 μg C-CO2 g-1 d-1 in D100, D200 and D300, respectively. After 30 days, CO2 evolution gradually decreased at 16 μg C-CO2 g-1 d-1, and the total production of C-CO2 was 440, 565, 1249 and 1673 μg C-CO2 g-1 in D0, D100, D200 and D300, respectively. The results show that an increase in the LCM dose will significantly increase CO2 production, following the pattern D300>D200>D100>D0. Gradually, during 30 days of pre-incubation treatment, CO2 production decreased until there were similar soil respiration levels, with the exception of D300, which has a significantly greater value. There were no significant observed differences in CO2 production with respect to the controls when dimethenamid was applied in the LCM treatments.
Amended soils were characterized by a large amount of fresh organic matter available for microorganisms, which increased with a greater LCM dose (Table 1). Figure 2 shows the relationship between the decreasing dissolved organic carbon and respiration rate levels.
The initial CO2 increase is essentially a result of the rapid biodegradation of the available carbon (Reinertsen et al., 1984; Ajwa and Tabatabai, 1994, Plaza et al., 2004.)
Enzymatic FDA activity is a sensitive and non-specific tool for representing the hydrolytic activity of soil micro-organisms. The FDA activity in each LCM-amended soil at different pre-incubation periods is presented in Table 2. FDA hydrolysis indicated high variability in the time between treatments. A statistical analysis was performed for each pre-incubated soil at each evaluation time. No significant differences were found in the LCM-amended soils when dimethenamid was applied; however, the application of LCM significantly increased FDA activity, with the highest dose of LCM observed for pre-incubated soils at 1, 10 and 20 days. The average FDA activity of soil was approximately 440 μg g-1 fluorescein. For D300, in the pre-incubated amended soils for 1, 10, 20 days, the FDA activity was approximately 460, 510 and 580 μg g-1 fluorescein, respectively; however, decreased after 20 days. For the 30 pre-incubated soils, FDA activity did not show any significant difference among treatments, except for D300, which had an average of 490 μg g-1 fluorescein. Similar results have been obtained from other authors who have shown that an increase in enzyme activity is related to the organic manure application and amendments (Perucci, 1992; Serra-Wittling et al. 1996).
Biological assays (microbiological respiration and FDA measurement) were used to determine the stabilisation of amended soils in comparison to non-amended soil. The results show that amended soils require more than 20 days to stabilise, which is the minimum time period required between LCM and herbicide application.
Both microbial respiration and enzymatic activity indicated that dimethenamid application at the recommended field dose did not display a significant difference among LCM treatments. This is most likely due to the dimethenamid is part of a family of herbicides that are not considered to be completely mineralisable (Stamper and Tuovinen, 1998; De Schrijver and De Mot, 1999).
3.2. Dimethenamid degradation in LCM-amended soils
The results of this study are shown in Figure 3. For each evaluation period, the 1 day pre-incubated soils, D200 and D300, did not significantly differ in residual concentration of dimethenamid. For example, approximately 60% of the dimethenamid was degraded at 10 days and 90% was degraded at 60 days. For soils pre- incubated for 10 days, D200 and D300 degrade at 92 and 97% of dimethenamid, respectively. This explains the effect of LCM dose and pre-incubation time in di-methenamid persistence compared to soil with 80% dimethenamid degradation. D100 amended soil has a behaviour similar to D0. After 20 days of pre-incubation, the degradation of dimethenamid is similar for all treatments at approximately 80%, except for D300, which undergoes 90% degradation.
The t1/2 of dimethenamid was significantly smaller for D200 and D300 in pre-incubated amended soils from days 1-20 (Table 3) and ranged from 13 to 21 days. For D0 and amended soils pre- incubated for 30 days, the dimethenamid half-life was approximately 27 days.
Our results indicate that dimethenamid application to the soil must be after the liquid cow manure reaches the stabilization step. Furthermore, our results suggest that dimethenamid degradation is significantly greater when larger liquid cow manure (LCM) doses are applied. This degradation is also affected by the period of pre-incubation time in amended soils due to microbial activity. Therefore, based on this study, dimethenamid application is recommended when the LCM-amended soils are stabilised microbiologically, which, as in non-amended soils, occurs at least after 20 days from LCM application.
This study was financed by the projects FONDECYT 1070568 and DIUFRO DI10-1002.
Adam, G., Duncan, H. 2001. Development of a sensitive and rapid method for the measurement of total microbial activity using fluorescein diacetate (FDA) in a range of soils. Soil Biol. Biochem. 33, 943-951. [ Links ]
Aguilera, P., Briceño, G., Candia M., Mora M., Demanet R., Palma, G. 2009. Effect of dairy manure rate and the stabilization time of amended soils on atrazine degradation. Chemosphere 77, 785-790. [ Links ]
Ajwa, H., Tabatabai, M. 1994. Decomposition of different organic materials in soils. Biol. Fertil. Soils 18, 175-182. [ Links ]
Albarrán, A., Celis, R., Hermosin, M.C., Lopez-Pineiro, A., Cornejo, J. 2004. Behaviour of simazine in soil amended with the final residue of the olive-oil extraction process. Chemosphere 54, 717-24. [ Links ]
Alef, K. 1995. Estimation of soil respiration. In: Alef, K., Nannipieri, P. (Eds.), Methods in Applied Soil Microbiology and Biochemistry. Academic Press, London, 464-467. [ Links ]
Anderson, K., Basile, J., Johnson, E. 2005. Analytical method for dimethenamid-P in selected raw agricultural commodities by gas chromatography with electron capture detection. J. AOAC Int. 88, 1428-1432. [ Links ]
Briceño, G., Palma, G., Durán, N. 2007. Influence of organic amendment on the biodegradation and movement of pesticides. Crit. Rev. Environ. Sci. and Technol. 37, 233-271. [ Links ]
Briceño, G., Demanet, R., Mora, ML., Palma, G. 2008. Effect of liquid cow manure on andisol properties and atrazine adsorption. J. Environ. Qual. 37, 1519-1526. [ Links ]
Briceño, G., Jorquera, M., Demanet, R., Mora, ML., Durán, N., Palma, G. 2010. Effect of cow amendment on atrazine dissipation and bacterial community structure in a agricultural Andisol. Sci. Total Environ. 408, 2833-2839. [ Links ]
Crawford, J., Sims, G., Simmons, F., Wax, L., Freedman, D. 2002. Dissipation of the herbicide [14C] dimethenamid under anaerobic conditions in flooded soil microcosms. J. Agric. Food Chem. 50, 1483-1491. [ Links ]
De Schrijver, A., De Mot, R. 1999. Degradation of pesticides by actinomycetes. Crit. Rev. Microbiol. 25, 85-119. [ Links ]
Dungan, R.S., Ibekwe, A.M., Yates, S.R. 2003. Effect of propargyl bromide and 1,3-dichloropropene on soil microbial communities. FEMS Microbiol. Ecol. 43, 75-87. [ Links ]
Farenhorst, A., Reimer, M., Londry, K., Saiyed, I. 2006. 2, 4-Dichlorophenoxy acetic acid mineralization in amended soil. J. Environ. Sci. Health B. 41, 509-522. [ Links ]
Hladik, M., Bouwer, E., Roberts, L. 2008. Neutral degradates of chloroacetamide herbicides: Occurrence in drinking water and removal during conventional water treatment. Water Res. 42, 4905-4914. [ Links ]
Moorman, T., Cowan, J., Arthur, E., Coats, J. 2001. Organic amendments to enhance herbicide bio-degradation in contaminated soils. Biol. Fertil. Soils 33, 541-545. [ Links ]
Nkedi-Kizza, P., Brown, K.D. 1998. Sorption, degradation and mineralization of carbaryl in soils for single pesticide and multiple pesticide systems. J. Environ. Qual. 27, 1318-1324. [ Links ]
Perrin-Ganier, C., Schiavon, F., Morel, J.L., Schiavon, M. 2001. Effect of sludge-amendment or nutrient addition on the biodegradation of the herbicide isoproturon in soil. Chemosphere 44, 887-92. [ Links ]
Perucci, P. 1992. Enzyme activity and microbial bio-mass in a field soil amended with municipal refuse. Biol. Fertil. Soils 14, 54-60. [ Links ]
Perucci, P., Dumontet, S., Bufo, S., Mazzatura, A., Casucci, C. 2000. Effects of organic amendent and herbicide treatment on soil microbial biomass. Biol. Fertil. Soils 32, 17-23. [ Links ]
Peters, J., Combs, S.M., Hoskins, B., Jarman, J., Kovar, J., Watson, M., Wolf, A., Wolf, N. 2003. Recommended Methods of Manure Analysis. University of Wisconsin Cooperative Extension Publication A3769. University of Wisconsin Cooperative Extension, Madison, WI. [ Links ]
Plaza, C., Hernández, D., García-Gil, J., Polo, A. 2004. Microbial activity in pig slurry-amended soils under semiarid conditions. Soil Biol. Biochem. 36, 1577-1585. [ Links ]
Reinertsen, S.A., Elliott, L.F., Cochran, V.L., Campbell, G.S. 1984. The role of available C and N in determining the rate of wheat straw decomposition. Soil Biol. Biochem. 16, 459-464. [ Links ]
Sadzawka, A., Grez, R., Carrasco, M., Mora, ML. 2006. Método de análisis recomendados para los suelo Chilenos. Comisión de Normalización y Acreditación Sociedad Chilena de la Ciencia del suelo. [ Links ]
Said-Pullicino, D., Gigliotti, G., Vella, A. 2004. Environmental fate of triasulfuron in soils amended with municipal waste compost. J. Environ. Qual. 33, 1743-1751. [ Links ]
Salazar,F., Dumont, J., Santana, M., Pain, B., Chad-wick, D. Owen, E. 2003. A surver of dairy effluent management in the south of Chile, Arch. Med. Vet. 34, 215-225. [ Links ]
Serra-Wittling, C., Hounot, S., Barriuso, E. 1996. Modification of soil water retention and biological properties by municipal solid waste compost. Compost Sci. Util. 4, 44-52 [ Links ]
Sluszny, C., Graber, E., Gerstl, Z. 1999. Sorption of s-triazine herbicides in organic matter amendment soils: fresh and incubated systems. Water Air Soil Pollut. 115, 395-410. [ Links ]
Stamper, D., Tuovinen, O. 1998. Biodegradation of the acetanilide herbicides alachlor, metolachlor and propachlor. Crit. Rev. Microbiol. 24, 1-10. [ Links ]
Topp, E., Tessier, L., Gregorich, E. 1996. Dairy manure incorporation stimulates rapid atrazine mineralization in an agricultural soil. Can. J. Soil Sci. 76, 403-409. [ Links ]