It is also used as part of combination formulations for rice (Singh et al., 2008; Saha & Rao, 2009). Chlorimuron-ethyl

selleck screening library exerts carry-over effects on succeeding crops such as sugar beet, corn and cotton. It reduced the yield of sugar beet planted 1 year after its application (Renner & Powell, 1991). Chlorimuron-residue haremed corn (Curran et al., 1991), and also harmed sunflower, watermelon, cucumber and mustard when observed 16 weeks after application (Johnson & Talbert, 1993). Although its persistence is moderate in soil [half-life (T1/2) 30 days], like many other sulfonylurea herbicides, its persistence increases with increasing pH. The T1/2 of chlorimuron under acidic conditions (pH 5) is 17–25 days, whereas at higher pH this may increase to 70 days. The half-life of chlorimuron in a silt-loam soil was 7 days at pH 6.3 and 18 days at pH 7.8 (Brown, 1990). By using a root bioassay technique, Schroeder (1994) determined the half-life of chlorimuron in soils of different pH-ranges as 12–50 days. Bedmar et al. (2006) observed a wide range of half-life for chlorimuron in soil from 30 days at pH 5.9 to 69 days at pH 6.8. Chlorimuron-ethyl degrades in the agricultural environment primarily via pH- and temperature-dependent chemical hydrolysis (Beyer et al., 1988; Brown, 1990; Hay, 1990), as observed for many sulfonylurea herbicides, such as sulfometuron-methyl (Harvey et al., LDE225 molecular weight 1985),

chlorsulfuron (Sabadie, 1990), metsulfuron-methyl (Sabadie, 1991), rimsulfuron (Schneiders et al., 1993), nicosulfuron (Sabadie, 2002) and flazasulfuron (Bertrand et al., 2003). The phototransformation of chlorimuron by sunlight also takes place on the soil Montelukast Sodium surface (Choudhury & Dureja, 1996a) and in water (Venkatesh et al., 1993; Choudhury & Dureja, 1996b). Within the surface soil chlorimuron is also considered to serve as a source of carbon, nitrogen and sulfur for microorganisms. There are reports on the utilization of sulfonylurea herbicides by microorganisms. The metabolic pathways for the degradation of chlorsulfuron and metsulfuron-methyl

by Streptomyces griseolus (Joshi et al., 1985; Reiser & Steiglitz, 1990), and trisulfuron by S. griseolus in artificial media (Dietrich et al., 1995) have been established. At low pH the degradation of trisulfuron-methyl takes place by chemical hydrolysis, whereas in neutral to alkaline soil, microorganisms play the dominant role in its degradation (Peeples et al., 1991), and the major degradation route is cleavage of the sulfonylurea bridge (Vega et al., 2000). Streptomyces griseolus can also de-esterify and O-dealkylate the chlorimuron-ethyl molecule (Reiser & Steiglitz, 1990). A bacterium, Pseudomonas sp., isolated from chlorimuron-ethyl-contaminated soil degrades the herbicide by cleaving the sulfonylurea bridge (Ma et al., 2009), and a yeast strain, Sporobolomyces sp., was isolated as a chlorimuron-degrading organism (Xiaoli et al., 2009).