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Soil metabolism of the herbicide rimsulfuron under laboratory and field conditions.

机译:实验室和田间条件下除草剂瑞草隆的土壤代谢。

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Procedures were developed for soil analysis of rimsulfuron and its metabolites by means of GC-ECD, GC-FPD and GC-MS, with a detection limit of 1μg of rimsulfuron equivalents per kilogram of dry soil, after purification of the soil extracts by TLC.Soil containing an exaggerated rimsulfuron concentration was incubated in the laboratory, in order to adjust the analytical procedures. To evaluate the role of different manuring treatments, rimsulfuron was applied postemergence (10 g ha-1 on a corn [maize] field at Melle, Belgium, in 1994 and 1995) on plots treated with (a) green manure, pig slurry applied in (b) November and (c) March, and cow manure applied in (d) November and (e) March and (f) untreated control plots without organic fertilizer. Neither rimsulfuron nor its metabolites were detected at soil depths lower than 8 cm. The results show that manure treatments prolong rimsulfuron half-life in the 0-8 cm surface soil layer from a minimum of 14 days (control) to a maximum of 46 days (pig slurry in March). At maize harvest, rimsulfuron and its metabolites were not detected in soil. Similar soil degradation pathways were observed in the field as in the laboratory. N-(4,6-dimethoxypyrimidin-2-yl)-N-[3-(ethylsulfonyl)-2-pyridinyl]urea was a transient soil degradation product. N-[3-(ethylsulfonyl)-2-pyridinyl]-4,6-dimethoxy-2-pyrimidineamine attained a maximum soil concentration after 20 days of incubation and then progressively disappeared and could not be detected after 40 days. The high-molecular weight amine did not accumulate in soil, eliminating the concern for potential formation of nitroso amino compounds. 2-Hydroxy-3-(ethylsulfonyl)pyridine (4) became the major rimsulfuron soil degradation product. The soil concentrations increased andattained a maximum after 40 days of incubation and then decreased; its isomerization into 2-pyridone, followed by hydrolysis, could transform it into low molecular weight non-toxic products. The concentrations of 2-amino-4,6-dimethoxypyrimidine were somewhat lower than those of compound (4).
机译:开发了用于通过GC-ECD,GC-FPD和GC-MS对利福隆及其代谢物进行土壤分析的程序,通过TLC纯化土壤提取物后,检测限为每公斤干土1μg利福隆当量。为了调整分析程序,在实验室中孵育了含有过量的嘧磺隆浓度的土壤。为了评估不同肥料处理的作用,在(a)绿肥处理,猪粪施肥处理后的地块上,于苗后(1994年和1995年在比利时梅勒的玉米[玉米]田间施用rimsulfuron)(10 g ha-1)。 (b)11月和(c)3月,在(d)11月和(e)3月和(f)未经处理的无有机肥料的对照地块施用牛粪。在低于8 cm的土壤深度均未检测到rimsulfuron及其代谢产物。结果表明,粪便处理可在0-8厘米表层土壤中延长rimsulfuron的半衰期,从最少14天(对照)到最多46天(3月的猪粪)。在玉米收获时,在土壤中未检测到瑞磺隆及其代谢产物。在田间观察到的土壤降解途径与实验室相似。 N-(4,6-二甲氧基嘧啶-2-基)-N- [3-(乙基磺酰基)-2-吡啶基]脲是一种短暂的土壤降解产物。 N- [3-(乙基磺酰基)-2-吡啶基] -4,6-二甲氧基-2-嘧啶胺在培养20天后达到最大土壤浓度,然后逐渐消失,在40天后无法检测到。高分子量胺没有在土壤中积累,消除了对亚硝基氨基化合物潜在形成的担忧。 2-羟基-3-(乙基磺酰基)吡啶(4)成为林磺隆土壤降解的主要产物。孵化40天后,土壤浓度增加并达到最大值,然后下降。其异构化为2-吡啶酮,然后水解,可将其转化为低分子量无毒产品。 2-氨基-4,6-二甲氧基嘧啶的浓度略低于化合物(4)的浓度。

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