Efficiency of the intestinal bacteria in the degradation of the toxic pesticide, chlorpyrifos
- 1.9k Downloads
Chlorpyrifos (CP) is the most commonly used pesticide throughout the world. Its widespread use in agriculture and its potential toxicity to humans from ingestion of CP contaminated food have raised concerns about its risk to health. Human intestinal microflora has the ability to degrade pesticides, but the exact mechanisms involved and the metabolite end-products formed are not well understood. The primary objective of this work was to analyse the in vitro degradation of CP by five model intestinal bacteria namely Lactobacillus lactis, L. fermentum, L. plantarum, Escherichia coli and Enterococcus faecalis. Plate assay results revealed that L. lactis, E. coli and L. fermentum could grow with high concentrations of CP (>1,400 μg/mL), whereas E. faecalis and L. plantarum could grow with concentrations as low as 400 and 100 μg/mL, respectively. The best three CP degraders were therefore used in further experiments. The degradation of CP-induced organophosphorous phosphatase (OPP) production and that OPP concentration were higher in the supernatant (extracellular) rather than inside the cells by factor of up to 28. L. fermentum degraded 70 % CP with 3,5,6-trichloro-2-pyridinol (TCP) detected as the end product. L.lactis degraded up to 61 % CP with chlorpyrifos oxon detected as the end product, whereas E.coli degraded a lesser concentration (16 %) to chlorpyrifos-oxon and diethylphosphate.
KeywordsChlorpyrifos Biodegradation Diethylthiophosphate Organophosphorous phosphatase
Chlorpyrifos [O,O-diethyl O-(3,5,6-trichloro-2-pyridinyl) phosphorothioate] (CP) is one of the most commonly used agricultural organophosphorous (OP) insecticides, which controls a broad spectrum of insects. Despite the recent regulatory decision of the United States to eliminate its residential use, CP continues to be widely used in agriculture in other regions of the world including Egypt, Germany, China, India, Bangladesh, Pakistan, and Iraq. CP acts by interfering with cholinesterase, an enzyme that is essential for the proper working of the nervous system of both humans and insects (Xu et al. 2008). The widespread use of CP in agriculture has raised public concerns about the potential human health risks that can be caused by the ingestion of CP-contaminated foods (Atif Randhawa et al. 2007). In general, CP can enter the human body through the skin (dermal exposure), mouth (oral exposure) and lungs (respiratory exposure). However, the transport of CP within the body depends on whether it is absorbed through the skin, lungs or gastrointestinal (GI) tract. CP absorbed through the GI tract, enters the blood stream and reaches the liver, the major site of pesticide metabolism, resulting in liver toxicity. Moreover, CP can also be accumulated in the body tissues, proteins, fats and bones for longer period of time causing additional health hazards (Environmental Risk assessment 2002). CP is degraded in soil and aquatic environment by chemical hydrolysis and by microbial activities. However, the rate of degradation by chemical hydrolysis is very low when compared to microbial degradation, and this could be attributed to the presence of efficient hydrolytic and oxidative enzymes which degrade these xenobiotic compounds (Munnecke 1976). The accessibility of the pesticide to the cell across the cell membrane is one of the most important considerations for degradation. Degradation of different pesticides can range from high to low because of accessibility issues. Hence, it is essential to study the location and function of the enzyme to understand its significance in degradation of studies. (Richnis et al. (1997) studied the surface-expressed organophosphorous hydrolase activity on the organophosphorous pesticide and found that more than 80 % of the activity was located on cell surface, but in case of Nocardiodes simplex NRRL B-24074 it was located as a distinct enzyme in the cytoplasm (Mulbry 2000). In most cases, aerobic bacteria tend to transform CP to produce diethylthiophosphate (DETP) and 3,5,6-trichloro-2-pyridinol (TCP) (Yang et al. 2006). However, the isolation and detailed studies of CP degrading bacteria have been difficult because TCP, the hydrolytic by-product of CP, is toxic to the growth of the degrading organism. The bacterium capable of using TCP as the sole carbon and energy source under aerobic conditions was identified as a Pseudomonas sp. (ATCC 700113), by Feng et al. (1997). Subsequently, other CP degrading bacteria such as Ralstonia sp. (Li et al. 2010), Lactobacillus brevis (Islam et al. 2009), Bacillus pumilus strain (Anwar et al. 2009), Pseudomonas aeruginosa, Bacillus cereus, Klebsiella sp. (Lakshmi et al. 2009), Paracoccus sp. (Xu et al. 2008) and Sphingomonas sp strain DSP-2 (Li et al. 2007) have been reported. L. lactis, L. plantarum, L. fermentum, E. faecalis and E.coli are intestinal bacteria which are reported to prevent major intestinal infections (Biller et al. 1995) and are involved in the alleviation of inflammatory bowel disease (Sartor 2004), production of antimicrobial substances (Servin 2004) and regulation of gastrointestinal immunity(Christensen et al. 2002). Along with this, it was reported by Zhao and Wang (2011) that Lactobacillus sp. can also degrade several organophosphorous pesticides like dimethoate, fenthion, malathion, methyl parathion, monocrotophos, phorate and trichlorphon but its action on CP has yet to be studied. Moreover, the role of CP degrading microflora and the site of CP degradation in the GI tract are also poorly understood (Rose et al. 2005). Here, we report on the degradation of CP by five model intestinal bacteria which included L. lactis, L. plantarum, L. fermentum, E.faecalis and E.coli.
Materials and methods
Pesticide and chemicals
Commercial-grade insecticide chlorpyrifos (50 % E.C) was purchased from Dow Agro Sciences, India Private Limited. Chlorpyrifos and 3,5,6-trichloro-2-pyridinol (TCP) were purchased from Sigma-Aldrich Co., USA. All other chemicals and media used in this study were purchased from Hi-Media Private Ltd, Mumbai, India.
Bacterial strains and media
Enterococcus faecalis (MTCC 2729), E. coli (MTCC 433), L. fermentum (MTCC 903), L. lactis (MTCC 4185), L. plantarum (MTCC 1325) were purchased from Microbial Type Culture Collection (MTCC) centre, Chandigarh, India. The strains were stored in Luria–Bertani (LB) medium containing 20 % glycerol at −20 °C. LB Agar was used for routine culturing of the strains. Chlorpyrifos degradation analyses were carried out in Minimal Salt broth (MS broth). MS broth contained (g/L) Yeast Extract 1, K2HPO4 1.5, KH2PO4 0.5 g, (NH4)2SO4 0.5, NaCl 0.5, MgSO4 0.2, CaCl2 0.05, FeSO4 0.02. 100 mg/L of chlorpyrifos was filter sterilized and used for degradation experiments (Yang et al. 2006).
Plate assay for chlorpyrifos
The maximum concentration of CP tolerated by the bacterial strains was determined by streaking the strains on MS agar plates containing various concentrations of chlorpyrifos 100–2,000 mg/L. All the plates were incubated for 37 °C until visible growth was observed (Shafiani and Malik 2003).
Extraction of crude enzyme and organophosphorous phosphatase (OPP) assay
The cells grown in MS broth containing 100 mg/L chlorpyrifos were harvested and pelleted by centrifugation at 8,000 rpm for 10 min. The supernatant was used to determine extracellular OPP activity. The cell pellet was resuspended in 50 mmol/L Tris–HCl (pH 8) buffer containing 0.1 mmol/L phenylmethylsulfonyl fluoride (PMSF) and sonicated for 10 times, each for 10 s duration with 15 s incubation on ice between sonication, using a Digital Sonifier (Bandelin Electronics, Berlin, Germany). The lysate was centrifuged at 10,000 rpm for 30 min and the supernatant was used to determine intracellular OPP activity (Wang et al. 2008). Protein concentrations were determined by the method of Lowry et al. (1951). All the experiments were repeated three times. OPP activity was measured by adding 100 μL of crude enzyme to 900 μL of Tris HCl (pH 9) containing 10 mg/mL p-nitrophenol phosphate and the mixture was incubated for 10 min at 37 °C. The reaction was terminated by addition of 1 mL of 10 % trichloroacetic acid and 1 mL of 10 % Na2CO3 and the liberated yellow coloured end product p-nitrophenol was measured in a Ultrospec™ 2100 pro spectrophotometer (GE Healthcare) at 410 nm. One unit (U) of OPP activity is defined as the amount of enzyme liberating 1 μmol of p-nitrophenol per minute at 37 °C (Alvarez-Macarie et al. 1999).
Degradation analysis by LCMS
Mid log phase culture (7 × 106) of the three strains was inoculated into MS broth containing 100 mg/L chlorpyrifos and incubated in a shaking incubator at 37 °C (Uninoculated MS broth containing 100 mg/L chlorpyrifos was used as a control). After 15 days of incubation, the optical densities of the cultures were measured (OD 610 nm). 50 mL culture aliquots and 50 mL uninoculated control medium aliquots were centrifuged at 7,000 rpm for 10 min and the supernatant was used for degradation analysis. For this, the supernatant was extracted with an equal volume of dichloromethane and the bottom organic layer was aspirated and dried at room temperature. The residue was then dissolved in HPLC grade acetonitrile and analysed using liquid chromatography–mass spectroscopy (LC–MS) (Prominence, SHIMADZU) (Anwar et al. 2009). The LC–MS was equipped with an inertsil ODS3 column (50 × 3 mm) and a UV detector. The cartridges were conditioned with acetonitrile and washed with deionized water containing 0.1 % formic acid. Sample injection volume was 10 μL and a gradient mobile phase containing acetonitrile and 0.1 % formic acid in water was used at a flow rate of 0.2 mL/min. The oven temperature was maintained at 37 °C and the UV detector at 230 nm. Under these conditions, the retention time for chlorpyrifos was 18.6 min. Mass spectroscopy (MS) was performed using a Finnegan model MS (Thermo electron corporation, USA). The ion trap detector with atomic pressure chemical ionization (APCI) source was used for quantification in positive ionization mode. The operating conditions were APCI source: spray voltage (kV)—5.02, capillary voltage (V) −16.96, capillary temperature (°C)—275, capillary temperature (°C)—270. Ion detection system: dynode (kV)—14.86, multiplier (V)—821.2.
Results and discussion
Plate assay and strain selection
Organophosphorous phosphatase (OPP) assay
Growth, organophosphorous phosphatase (OPP) activity and chlorpyrifos degradation
Growth (OD 610 nm)
OPP activitya (U)
Analysis of chlorpyrifos degradation and end product metabolites by LC–MS
Chlorpyrifos is known to be absorbed to surfaces. Nolan et al. (1984) studied the rate of chlorpyrifos absorption by oral administration of pesticide to humans and determined that 70 % was absorbed within 48 h whereas in rats and mice this took a little longer (48–60 h) (Ahdaya et al. 1981). Smith et al. (1967) reported that chlorpyrifos residues were predominantly deposited in fatty tissues. The rate of adsorption, deposition and excretion of chlorpyrifos in humans is a delayed process, and so it should be monitored for a long time to make the study relevant. The optical density and the percentage of chlorpyrifos degraded are given in Table 1. At the end of 15 days, the optical densities of L. lactis, L. fermentum and E. coli were determined to be 0.59, 0.94 and 1.12, respectively, at which time 61, 70 and 16 % chlorpyrifos was degraded, respectively. Interestingly, though E. coli had the highest culture density, CP degradation was the lowest. This would suggest that the strains either produced different metabolic end products and/or could tolerate the toxic effects of the same end products to varying degrees.
Xu et al. (2010) had showed that the intestinal microorganisms were efficient in degrading toxic food grade sudan dyes and our studies reported here have extended this to include CP. Our present studies have shown that L. lactis, L. fermentum and E. coli isolates from the gastrointestinal tract can degrade CP. The end product degradation profiles and/or the types of end products are different in all the three strains, which suggest that different pathways may be operating in these strains. The individual role of bacterial strains on chlorpyrifos in the in vitro condition was analysed, but the role in the in vivo as well as efficiency of the strains in consortium needs to investigate. Future studies should also target CP degradation by other gut microbes and also focus on the possible synergistic mineralisation of the end products by other gut microbes.
The authors are thankful to Dr. T. Kumar Mass spectra analyst for the interpretation of mass spectra results and the facilities provided by SRM University to support this work.
- Environmental Risk assessment (2002) Review of chlorpyrifos poisoning data. US ERA1-46Google Scholar
- Feng Y, Racke KD, Bollag JM (1997) Isolation and characterization of chlorinated-pyridinol-degrading bacterium. Appl Environ Microbiol 63:4096–4098Google Scholar
- Lowry OH, Rosebrough NJ, Farr AL, Randall RJ (1951) Protein measurement with the folin phenol reagent. J Biol Chem 193(1):256–275Google Scholar
- Mulbry W (2000) Characterization of a novel organophosphorous hydrolase from Nocardiodes simplex NRRL B-24074. Microbiol Res 154:285–308Google Scholar
- Munnecke DM (1976) Enzymatic hydrolysis of organophosphate insecticides, a possible pesticide disposal method. Appl Environ Microbiol 32:7–13Google Scholar
- Nolan RJ, Rick DL, Freshour NL, Saunders JH (1984) Chlorpyrifos: pharmacokinetics in human volunteers. Toxico1 Appl Pharmacol 73(1):8–15Google Scholar
- Rose RL, Tang J, Choi J, Cao Y, Usmani A, Cherrington N, Hodgson E (2005) Pesticide metabolism in humans including polymorphisms. Scand J Work Environ Health 31:156–163Google Scholar
- Wang JF, Gao MH, Wu NF, Pan CP (2008) The degradation effects of a Pseudomonas hydrolase OPHC2 to organophosphorus insecticides. J Environ Sci 183(2–3):804–810Google Scholar
- Zhao XH, Wang J (2011) A brief study on the degradation kinetics of seven organophosphorus pesticides in skimmed milk cultured with Lactobacillus sp. at 42 °C. Food Chem 313(1):300–304Google Scholar
This article is published under license to BioMed Central Ltd. Open Access This article is distributed under the terms of the Creative Commons Attribution License which permits any use, distribution and reproduction in any medium, provided the original author(s) and source are credited.
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 2.0 International License (https://creativecommons.org/licenses/by/2.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.