Transport and distribution of lindane and simazine in a riverine environment: measurements in bed sediments and modelling

Aquatic sediments often remove hydrophobic contaminants from fresh waters. The subsequent distribution and concentration of contaminants in bed sediments determines their effect on benthic organisms and the risk of re-entry into the water and/or leaching to groundwater. This study examines the transport of simazine and lindane in aquatic bed sediments with the aim of understanding the processes that determine their depth distribution. Experiments in flume channels (water flow of 10 cm s(-1)) determined the persistence of the compounds in the absence of sediment with (a) de-ionised water and (b) a solution that had been in contact with river sediment. In further experiments with river bed sediments in light and dark conditions, measurements were made of the concentration of the compounds in the overlying water and the development of bacterial/algal biofilms and bioturbation activity. At the end of the experiments, concentrations in sediments and associated pore waters were determined in sections of the sediment at 1 mm resolution down to 5 mm and then at 10 mm resolution to 50 mm depth and these distributions analysed using a sorption-diffusion-degradation model. The fine resolution in the depth profile permitted the detection of a maximum in the concentration of the compounds in the pore water near the surface, whereas concentrations in the sediment increased to a maximum at the surface itself. Experimental distribution coefficients determined from the pore water and sediment concentrations indicated a gradient with depth that was partly explained by an increase in organic matter content and specific surface area of the solids near the interface. The modelling showed that degradation of lindane within the sediment was necessary to explain the concentration profiles, with the optimum agreement between the measured and theoretical profiles obtained with differential degradation in the oxic and anoxic zones. The compounds penetrated to a depth of 40-50 rum over a period of 42 days. (C) 2004 Society of Chemical Industry.

Lindane induced cellular dysfunction in MDCK cells: The role of the peripheral benzodiazepine receptor

The central nervous system GABAA/Benzodiazepine (GABAA/BZD) receptors are targets for many pharmaceutical agents and several classes of pesticides. Lindane is an organochlorine pesticide, although banned from production in the U.S. since 1977, still imported for use as an insecticide and pharmaceutically to control ectoparasites (ATSDR, 1994). Lindane functions as a GABA/BZD receptor antagonist within the central nervous system (CNS). Outside of the CNS, peripheral BZD receptors have been localized to the distal tubule of the kidney. Previous research in our laboratory has shown that incubation of renal cortical slices with lindane can produce an increase in kallikrein leakage, suggesting a distal tubular effect. In this study, Madin Darby Canine Kidney (MDCK) cells were used as an in vitro system to assess the toxicity of lindane. This purpose of this study was to determine if interactions between a renal distal tubular BZD-like receptor and lindane could lead to perturbations in renal distal cellular chloride (Cl−) transport and mitochondrial dysfunction and ultimately, cellular death. ^ Pertubations in renal chloride transport were measured indirectly by determining if lindane altered cell function responsiveness following osmotic stress. MDCK cells pre-treated with lindane and then subjected to osmotic stress remained swollen for up to 12 hours post-stress. Lindane-induced dysfunction was assessed through stress protein induction measured by Western Blot analysis. Lindane pretreatment delayed Heat Shock Protein 72 (HSP72) induction by 36 hours in osmotically stressed cells. Pretreatment with 1 × 10 −5 M LIN followed by osmotic stress elevated p38 and Stress Activated Protein Kinase (SAPK/JNK) at 15 minutes which declined at 30 minutes. Lindane appeared to have no effect on Endoplasmic Reticulum Related Kinase (ERK) induction. Lindane did not effect osmotically stressed LLC-PKI cells, a control cell line. ^ Lindane-treated MDCK cells did not exhibit necrosis. Instead, apoptosis was observed in lindane-treated MDCK cells in both time- and dose-dependent manners. LLC-PKI cells were not affected by LIN treatment. ^ To better understand the mechanism of lindane-induced apoptosis, mitochondrial function was measured. No changes in cytochrome c release or mitochondrial membrane potential were observed suggesting the mitochondrial pathway was not involved in lindane-induced apoptosis. ^ Further research will need to be conducted to determine the mechanism of lindane-induced adverse cellular effects. ^

Evaluation of oxidative damage and renal distal tubule cell stress response following exposure to lindane

Lindane, or γ-hexachlorocyclohexane, is a chlorinated hydrocarbon pesticide that was banned from U.S. production in 1976, but until recently continued to be imported and applied for occupational and domestic purposes. Lindane is known to cause central nervous system (CNS), immune, cardiovascular, reproductive, liver, and kidney toxicity. The mechanism for which lindane interacts with the CNS has been elucidated, and involves antagonism of the γ-aminobutyric acid/benzodiazepine (GABAA/BZD) receptor. Antagonism of this receptor results in the inhibition of Cl- channel flux, with subsequent convulsions, seizures, and paralysis. This response makes lindane a desirable defense against arthropod pests in agriculture and the home. However, formulation and application of this compound can contribute to human toxicity. In conjunction with this exposure scenario, workers may be subject to both heat and physical stress that may increase their susceptibility to pesticide toxicity by altering their cellular stress response. The kidneys are responsible for maintaining osmotic homeostasis, and are exposed to agents that undergo urinary excretion. The mechanistic action of lindane on the kidneys is not well understood. Lindane, in other organ systems, has been shown to cause cellular damage by generation of free radicals and oxidative stress. Previous research in our laboratory has shown that lindane causes apoptosis in distal tubule cells, and delays renal stress response under hypertonic stress. Characterizing the mechanism of action of lindane under conditions of physiologic stress is necessary to understand the potential hazard cyclodiene pesticides and other organochlorine compounds pose to exposed individuals under baseline conditions, as well as under conditions of physiologic stress. We demonstrated that exposure to lindane results in oxidative damage and dysregulation of glutathione response in renal distal tubule (MDCK) cells. We showed that under conditions of hypertonic stress, lindane-induced oxidative stress resulted in early onset apoptosis and corresponding down-regulated expression of the anti-apoptotic protein, Bcl-xL. Thus, the interaction of lindane with renal peripheral benzodiazepine receptors (PBR) is associated with attenuation of cellular protective proteins, making the cell more susceptible to injury or death. ^

Guidance for the reregistration of pesticide products containing as the active ingredient lindane : case no. 0315 /

"EPA RS-85-027"--Cover.

The biologic and economic assessment of Lindane : a report of the Lindane assessment team to the rebuttable presumption against registration of Lindane, submitted to the Environmental Protection Agency on March 19, 1980 /

In cooperation with State agricultural experiment stations, Cooperative Extension Services, other state agencies, U.S. Envioronmental Protection Agency.

Metals and pesticide levels found in fish taken from Vancouver Lake: memorandum to Steve O'Brien, dated May 19, 1977

The Vancouver Lake Pilot Dredge Study revealed concentrations of certain chemicals which could be of concern: the metals copper, zinc and mercury and the pesticides lindane and aldrin were found in significant amounts. (PDF contains 1 page)

Organochlorine insecticide residues in sediments from the coast of Chittagong, Bangladesh

A total of 5 samples of marine sediments were analyzed for residues of organochlorine insecticide from the coast of Chittagong, Bangladesh. The analytical method consisted of 3 phases, extraction, clean-up and, analysis through Gas Chromatography (GC) with Electron Capture Detector (ECD). The concentration ranges were as follows 0.18 - 1.33 ng.g¹ for aldrin, 0.2 - 1.84 ng.g¹ for dielddrin, 0.30 - 1.31 ng.g¹ for endrin, 0.11 - 0.26 ng.g¹ for lindane, 0.56- 3.36 ng.g¹ for heptachlor, 0.2- 1.51 ng.g¹ for P,P' DDE, 0.18- 2.91 ng.g¹ for P,P' DDD, 0.11 - 3.12 ng.g¹ for P,P' DDT. These results reveal that the sediments along coast of Chittagong are slightly contaminated with some of these organochlorine insecticides.

The toxicity of four insecticides and a herbicide under tropical conditions

The toxicities of four insecticides and a herbicide to Tilapia macrochir were tested in the laboratory. The 24 hour LC50's were estimated as follows: Endrin 20% ,0.008 ppm; Lindane 5% granules, 4.6 ppmm; Synexa 50 (HCH) 50%), 5.6 ppm; Synex 25 (HCH 25%), 14.8 ppm; TOK herbicide (Nitrofen), 100% survival for 24 hours at 100 ppm. These estimates agree with results obtained by other workers elsewhere in the world. The laboratory determination of toxicity is important in estimating the direct effects of poisonous substances on fish, but other indirect effects may result from their use. These should be investigated in the field.

Organochlorine micropollutants in the Jiulong River Estuary and Western Xiamen Sea, China

Organochlorine contaminants including 12 polychlorinated biphenyl (PCB) congeners and 18 insecticides were determined in water, pore water and sediments of the Jiulong River Estuary and Western Xiamen Sea, China. The results showed that the levels of the total PCBs ranged from non-detectable to 1500 ngl(-1) in water, from 209 to 3870 ngl(-1) in pore water, and from 2.78 to 14.8 ng g(-1) dry weight in sediments. Total organochlorine insecticide concentrations were from below the limit of detection to 2480 ngl(-1) in water, from 267 to 33400 ngl(-1) in pore water, and from 4.22 to 46.3 ng g(-1) dry weight in sediments. Concentrations of PCBs and insecticides in pore water were significantly higher than those in surface water, due to the high affinity of these hydrophobic compounds for sediment phase. The PCB congeners with the highest concentrations were CB153, CB180 and CB194, which together accounted for 68-87% of total PCBs in water, pore water and sediment. Among the hexachlorocyclohexane (HCH) compounds, beta-HCH was found to be a major isomer. Analysis of 1,1,1-trichloro-2,2-bis-chlorophenyl-ethane (DDT) and its metabolites showed that 1, 1-dichloro-2[o-chlorophenyl]-2[p-chlorophenyl]-ethylene (DDE) was dominant in the group. In comparison to a 1998 study in the Western Xiamen Sea, levels of organochlorines were enhanced due probably to recent inputs and changes in sediments. (c) 2004 Elsevier Ltd. All rights reserved.

Micro-organic compounds in the Humber rivers

The concentrations of a range of micro-organic compounds in the Humber rivers have been measured at weekly intervals over a period of 1 year. The compounds include the triazine herbicides (simazine, atrazine, propazine, desmetryn and prometryn), selected organophosphorus insecticides (fenitrothion, malathion and parathion), phenylurea (chlorotoluron, diuron, isoproturon and linuron) and phenoxyacid herbicides (2,4-D, MCPA, MCPB and mecoprop), phenol derivatives (phenol, 2-ethylphenol, 2-chlorophenol, 4-nitrophenol, 2-methylphenol, 4-ethylphenol and 2,4-dichlorophenol), organochlorine insecticides (HEOD, DDT, TDE, DDE, HCB, alpha-BHC and lindane), PCB's and some synthetic pyrethroid insecticides (cis/trans-permethrin, fenvalerate and cypermethrin). The results indicate the high frequency of occurrence of many compounds in the southern Humber rivers Aire, Calder, Trent and Don compared with the more occasional concentrations found in the upland rivers with catchments dominated by low intensity agriculture. The more water soluble herbicides, atrazine, simazine, isoproturon and diuron are detected frequently in the southern rivers with the highest concentrations and abundance in the rivers Aire, Calder and Trent. The most abundant phenolic compound is 2,4-dichlorophenol usually occurring at concentrations <1 mu g/l. The organochlorine insecticides and PCB's are generally at concentrations <0.01 mu g/l, cis/trans-permethrin are the only synthetic pyrethroids detected and these are found in the rivers Aire and Calder at about equal concentrations of between 0.01 and 0.11 mu g/l. The results of the occurrence of simazine and atrazine in the rivers Trent, Don and Aire illustrate peaks in concentration in the spring and then later in the year during the early autumn coinciding with the first major storm after the summer. In the rivers Trent and Don, the annual exports (March 1994-95) of atrazine are lower than for simazine whereas in the R. Calder the yield of atrazine is higher than for simazine suggesting differences in use in these catchments. The maximum triazine concentration observed, i.e. 8 mu g/l of atrazine in the R. Calder, could have inhibiting effects on the phytoplankton and algal growth, although because of the transient nature of the peaks, recovery is expected to be rapid. The only other compounds measured at concentrations likely to produce detrimental ecotoxicological effects are cis/trans permethrin in the rivers Aire and Calder. (C) 1997 Elsevier Science B.V.

Modelling the fate of persistent organic pollutants (POPs) in the North Sea system

The environmental fate of selected persistent organic pollutants (POPs) in the North Sea system is modelled with a high resolution Fate and Transport Ocean Model (FANTOM) that uses hydrodynamic model output from the Hamburg Shelf Ocean Model (HAMSOM). Large amounts of POPs enter the North Sea from the surrounding highly populated, industrialised and agricultural countries. Major pathways to the North Sea are atmospheric deposition and river inputs, with additional contributions coming from bottom sediments and adjacent seas. The model domain covers the entire North Sea region, extending northward as far as the Shetland Islands, and includes adjacent basins such as the Skagerrak, Kattegat, and the westernmost part of the Baltic Sea. Model resolution (for both models) is 1.5’ latitude x 2.5’ longitude (approximately 3 km horizontal resolution) with 30 vertical levels. The POP model also has 20 sediment layers. Important model processes controlling the fate of POPs in the North Sea system are discussed. Results focus on Lindane gamma- HCH or gamma-hexachlorocyclohexane) and PCB 153.