Effects of water quality and fish size on toxicity of methiocarb, a carbamate pesticide, to rainbow trout

The acute toxicity of methiocarb in juvenile rainbow trout (Oncorhynchus mykiss, 3.25±0.79g) was evaluated in glass aquaria under static conditions. Nominal concentrations of methiocarb in the toxicity test ranged from 1.25 to 7.50mgL(-1). The concentrations of methiocarb that killed 50% of the rainbow trout within 24-h (24-h LC(50)), 48-h LC(50), 72-h LC(50), and 96-h LC(50) were 5.43±0.19, 5.04±0.18, 4.95±0.19, and 4.82±0.21mgL(-1) (95% confidence limits), respectively. Mortality of fish increased with increasing water temperature. Increasing alkalinity from 19mgL(-1) as CaCO(3) to 40, 60, or 90mgL(-1) as CaCO(3) significantly decreased mortality of fish. Total hardness ranging from 50mgL(-1) as CaCO(3) to 147mgL(-1) as CaCO(3) did not affect mortality of fish exposed to methiocarb. Fish exposed to methiocarb had histological alterations such as lamellar edema, separation of epidermis from lamellae, and lamellar fusion. Methiocarb exposed fish had necrosis between molecular and granular layer of cerebellum where Purkinje cells present. Results indicate that alkalinity, temperature, and fish size affect methiocarb toxicity of rainbow trout.     

Acute toxicity to freshwater organisms of antiparasitic drugs for veterinary use

The acute toxicity of five antiparasitic drugs used in the veterinary field-amprolium hydrochloride (APH), bithionol (BT), levamisole hydrochloride (LVH), pyrimethamine (PYM) and trichlorfon (TRC)-to the aquatic organisms Oryzias latipes, Daphnia magna, and Brachionus calyciflorus was examined. The toxicity test with O. latipes was conducted in accordance with the OECD Guidelines for the Testing of Chemicals (1993) to determine the 24-, 48-, 72-, and 96-h LC(50) values. In addition, 24- and 48-h EC(50) values for D. magna and a 24-h EC(50) for B. calyciflorus were determined with the DAPHTOXKIT F(trade mark) magna (Creasel, Belgium) and the ROTOXKIT F(trade mark) (Creasel, Belgium), respectively. High-performance liquid chromatographic analysis revealed that APH, LVH, and PYM were stable in water, but BT was unstable, decreasing by 84% on average at 24 h. TRC rapidly decomposed, with only 0.7% of the initial concentration remaining after 96 h, forming dichlorvos. The toxicity of TRC to O. latipes was determined in two ways: exposure to the same medicated water for 96 h (static test) and exposure to medicated water replaced every 24 h (semistatic test). AMP, LVM, and PYM were tested in the static condition, and BT was tested in the semistatic condition. BT was most toxic to O. latipes, with a 96-h LC(50) of 0.24 mg L(-1), followed by PYM, with a 96-h LC(50) of 5.6 mg L(-1). The 24-, 48-, 72-, and 96-h LC(50) values of TRC in the static test were 92.0, 45.2, 29.5, and 17.6 mg L(-1), respectively, which tended to be lower than those in the semistatic test, especially late in the observation period. D. magna was the most susceptible to TRC, with a 48-h EC(50) as low as 0.00026 mg L(-1). The 48-h EC(50) values of BT, PYM, and LVH for D. magna were 0.3, 5.2, and 64.0 mg L(-1), respectively. B. calyciflorus was the most susceptible to BT, with an EC(50) of 0.063 mg L(-1), followed by PYM, with an EC(50) of 15.0 mg L(-1). Among the test compounds, APH was the least toxic to all the freshwater organisms tested, with a 96-h LC(50) of >600 mg L(-1) for O. latipes, a 48-h EC(50) of 227 mg L(-1) for D. magna, and an EC(50) of 403 mg L(-1) for B. calyciflorus.     

Toxicity of binary chemical munition destruction products: methylphosphonic acid, methylphosphinic acid, 2-diisopropylaminoethanol, DF neutralent, and QL neutralent

This paper reports the toxicity and environmental impact of neutralents produced from the hydrolysis of binary chemical agent precursor chemicals DF (methylphosphonic difluoride) and QL (2-[bis(1-methylethyl)amino]ethyl ethyl methylphosphonite). Following a literature review of the neutralent mixtures and constituents, basic toxicity tests were conducted to fill data gaps, including acute oral and dermal median lethal dose assays, the Ames mutagenicity test, and ecotoxicity tests. For methylphosphonic acid (MPA), a major constituent of DF neutralent, the acute oral LD(50) in the Sprague-Dawley rat was measured at 1888 mg/kg, and the Ames test using typical tester strains of Salmonella typhimurium and Escherichia coli was negative. The 48-h LC(50) values for pH-adjusted DF neutralent with Daphnia magna and Cyprinodon variegatus were > 2500 mg/L and 1593 mg/L, respectively. The acute oral LD(50) values in the rat for QL neutralent constituents methylphosphinic acid (MP) and 2-diisopropylaminoethanol (KB) were both determined to be 940 mg/kg, and the Ames test was negative for both. Good Laboratory Practice (GLP)-compliant ecotoxicity tests for MP and KB gave 48-h D. magna EC(50) values of 6.8 mg/L and 83 mg/L, respectively. GLP-compliant 96-h C. variegatus assays on MP and KB gave LC(50) values of 73 and 252 mg/L, respectively, and NOEC values of 22 and 108 mg/L. QL neutralent LD(50) values for acute oral and dermal toxicity tests were both > 5000 mg/kg, and the 48-h LD(50) values for D. magna and C. variegatus were 249 and 2500 mg/L, respectively. Using these data, the overall toxicity of the neutralents was assessed.     

Dependency of copper toxicity to polychaete larvae on algal concentration

Algae are often used as food in aquatic metal toxicity tests to maintain the well-being of test animals. Such food addition may change metal bioavailability because of the reduction of aqueous metal concentration and the increase in particle-bound metal concentration. While the importance of aqueous exposure pathway is widely recognized, few studies have determined the contribution of the dietary pathway to the overall metal toxicity to aquatic invertebrates. In this study, we determined the toxicity of both algal-bound copper alone and copper solution containing algae to the larvae of marine polychaete Hydroides elegans. Algae that had been pre-exposed to copper at up to 1024 microg l(-1), when fed to the larvae, did not cause significant abnormal larval development. However, when larvae were exposed to algal-copper mixture, percentage of normal larvae could be modeled as a logistic function of aqueous copper concentration, with a 48-h EC(50) (mean +/- S.E.) of 64.9 +/- 4.8 microg Cul(-1). When the toxicity was expressed using total copper concentration, the EC(50) ranged from 58.4 +/- 4.5 microg l(-1) in the control to 121.9 +/- 9.9 microg l(-1) in the 10(6) cells ml(-1) algal treatment. This study highlights the dependency of copper toxicity on the aqueous exposure pathway in this polychaete and the importance of considering algal binding of the metal in larval toxicological tests.     

Toxicity of the molluscicidal plant, Ambrosia maritima L., to aquatic non-target organisms

The toxicity of the molluscicidal plant, Ambrosia maritima L., has been evaluated in fish, crustacea and algae. The LC50 for fries of the guppy, Lebistes reticulatus, was respectively 650 and 450 mg/litre using a powder or an ether-methanol-hexane extract from the leaves of the plant. This concentration is much higher than the molluscicidal concentration (LC90) of 35 to 70 mg/litre, which is used in the field (irrigation canals in Egypt). Preliminary tests showed that juveniles of L. reticulatus and Tilapia aurea were as sensitive as the fries. Using the same extract of A. maritima the LC50 for Daphnia magna was 766 mg/litre and no toxic effects could be observed in algae Selenastrum capricornutum at 1 g/litre. It can be concluded that A. maritima has a very low toxicity to aquatic non-target organisms. It is not toxic when used at the molluscicidal concentration of 35 to 70 mg/litre.     

Chlorosilane acute inhalation toxicity and development of an LC50 prediction model

The acute inhalation toxicity of 10 chlorosilanes was investigated in Fischer 344 rats using a 1-h whole-body vapor inhalation exposure and a 14-day recovery period. The median lethal concentration (LC50(1)) for each material was calculated from the nominal exposure concentrations and mortality. Experimentally derived LC50(1) values for monochlorosilanes (4257-4478 ppm) were greater than those for dichlorosilanes (1785-2092 ppm), which were greater than those for trichlorosilanes (1257-1611 ppm). Apparent was a strong structure-activity relationship (r2 = .97) between chlorine content and LC50(1) value. Estimated LC50(1) values for mono-, di-, and trichlorosilanes were determined to be 3262, 1639, and 1066 ppm, respectively, utilizing this relationship and the lower limit of the 95% prediction interval. The LC50(1) values determined in this series of studies were greater than that reported for hydrogen chloride (3124 ppm), when expressed on a chlorine equivalence basis (3570-5248 ppm), demonstrating that the acute toxicity of these chlorosilanes is similar to or less than that for hydrogen chloride. The good correlation between chlorine content and LC50(1) provides a sound basis for estimation of LC50(1) for chlorosilanes not already evaluated. The use of structure-activity relationships is consistent with the chemical industry and federal agency initiatives to reduce, refine, and/or replace the use of animals in testing without compromising the quality of health and safety assessments.     

Hazard/Risk Assessment of Pyridaben: II. Outdoor Aquatic Toxicity Studies and the Water-Effect Ratio

Outdoor acute aquatic toxicity studies with pyridaben and bluegill sunfish (Lepomis macrochirus) and mysid (Mysidopsis bahia) showed that the 96-h LC50s in site-specific water were significantly greater than in classical laboratory studies. In addition, outdoor acute studies showed that pyridaben degrades rapidly in water, in hours, which supports other laboratory and field studies on the fate of pyridaben in aquatic systems. Chronic toxicity to aquatic organisms is not an issue after application in the field because exposures will be brief. The water-effect ratio (WER) of site-specific to laboratory-water 96-h LC50s for L. macrochirus and M. bahia were 18.5 and 24.5, respectively. The lowest WER was used as an application factor with the laboratory LC50 values of several other aquatic organisms to develop adjusted site-specific LC50 values. Comparison of the distribution of adjusted LC50 values with a distribution of potential environmental exposure concentrations for pyridaben in water indicates minimal acute risk to aquatic organisms. When only acute laboratory data are available, the WER approach is a relevant and realistic means for determining an application factor and for estimating the aquatic hazard/risk assessment of non-persistent pesticides, because it considers a host of factors that affect bioavailability and subsequent toxicity.     

Toxicity of nitrite to three species of freshwater invertebrates

Nitrite is a compound with a high toxicity to aquatic animals. Several anthropogenic pollution sources are increasing the concentrations of this component of the nitrogen cycle. Despite this toxicity, there is little available literature on its effects on freshwater invertebrates. Laboratory bioassays were performed to obtain data on the lethal effects of nitrite to three species of freshwater invertebrates: the planarian Polycelis felina and the amphipods Echinogammarus echinosetosus and Eulimnogammarus toletanus. The LC(50), LC(10), and LC(0.01) values (mg/L NO(2)--N) at 24, 48, 72, and 96 h were calculated for each species. E. toletanus and E. echinosetosus were the most sensitive species, with 96 h LC(50) values of 2.09 and 2.59 mg/L NO(2)--N, respectively. In contrast, the planarian P. felina showed a higher tolerance to nitrite, with a 96 h LC(50) value of 60.0 mg/L NO(2)--N. The obtained results were compared with the reported nitrite data for other freshwater invertebrates. This study may contribute to a more appropriate assessment of the ecological risk of this compound in freshwater ecosystems.     

Physiology is pivotal for interactions between salinity and acute copper toxicity to fish and invertebrates

The present paper presents original data and a review of the copper (Cu) toxicity literature for estuarine and marine environments. For the first time, acute Cu toxicity across the full salinity range was determined. Killifish, Fundulus heteroclitus, eggs were hatched in freshwater (FW), 2.5, 5, 10, 15, 22 and 35 ppt (seawater, SW) and juveniles were allowed to acclimate for 7 days prior to acute toxicity testing. Sensitivity was highest in FW (96 h LC50: 18 microg/l), followed by SW (96 h LC50: 294 microg/l) with fish at intermediate salinities being the most tolerant (96 h LC50 > 963 microg/l at 10 ppt). This approximately 50-fold, non-linear variation in sensitivity could not be accounted for by Cu speciation or competition among cations but can be explained by physiology. The relative Na(+) gradient from the blood plasma to the water is greatest in FW followed by SW and is smallest at 10 ppt. Regression of Cu toxicity versus the equilibrium potential for Na(+), which reflects the relative Na(+) gradient, revealed that 93% of the variation can be attributed to Na(+) gradients and thus osmoregulatory physiology. Examination of the existing literature on acute Cu toxicity in SW (defined as >25 ppt) confirmed that early life stages generally are most sensitive but this pattern may be attributable to size rather than developmental stage. Regardless of developmental stage and phylogeny, size clearly matters for Cu sensitivity. The existing literature on the influence of salinity on acute Cu toxicity as well as studies of mechanisms of Cu toxicity in fish and invertebrates are reviewed.     

Effects of chlordane and lindane on testosterone and vitellogenin levels in green neon shrimp (Neocaridina denticulata)

The purpose of this study was to investigate the acute toxicity of chlordane and lindane as well as their endocrine disruption effect on green neon shrimp (Neocaridina denticulata), a common habitant in freshwater system of eastern Asia and Hawaii. First, the organisms were exposed to chlordane and lindane to estimate the 96-h LC(50)(96-h median lethal concentration). Then, levels of testosterone and vitellogenin in hemolymph of N. denticulata after exposure to sublethal concentrations of chlordane (1 ng/L and 10 ng/L) and lindane (0.1 microg/L and 1 microg/L) were also examined. The 96-h LC(50) values obtained from the results of acute exposure were 127.03 (130.11-122.35) ng/L and 9.36 (8.00-10.96) microg/L for chlordane and lindane, respectively. Furthermore, reductions of testosterone concentration were observed in both chlordane- and lindane-treated shrimps, whereas induction of vitellogenin-like protein was only apparent in chlordane-treated shrimps. Thus, it is concluded that chlordane and lindane may probably show some disruption endocrine functions on N. denticulata.     

Toxicity of perfluorooctane sulfonate and perfluorooctanoic acid to plants and aquatic invertebrates

Acute toxicities of perfluorooctane sulfonate (PFOS) and perfluorooctanoic acid (PFOA) were tested on four freshwater species and three plant species. PFOS was more toxic than PFOA for all species tested in this study. Similar time-response patterns of PFOS and PFOA toxicity were observed for each tested species. Values of the 48-h LC(50) of PFOS for all test species ranged from 27 to 233 mg/L and values of the 96-h LC(50) for three of the species ranged from 10 to 178 mg/L. Values of the 48-h LC(50) of PFOA for all test species ranged from 181 to 732 mg/L and values of the 96-h LC(50) for three of the species ranged from 337 to 672 mg/L. The most sensitive freshwater species to PFOS was green neon shrimp (Neocaridina denticulate) with a 96-h LC(50) of 10 mg/L. Of the aquatic organisms tested, the aquatic snail (Physa acuta) always has the highest resistance to PFOS or PFOA toxicity over each exposure period. Both PFOS and PFOA had no obvious adverse effect on seed germination for all three plant species. Five-day EC(50) of root elongation was more sensitive to LC(50) of seed germination in this study. Based on EC(10), EC(50), and NOECs, the 5-day root elongation sensitivity of test plants to both PFOS and PFOA was in the order of lettuce (Lactuca sativa) > pakchoi (Brassica rapa chinensis) > cucumber (Cucumis sativus). Based on the results of this study and other published literature, it is suggested that current PFOS and PFOA levels in freshwater may have no acute harmful ecological impact on the aquatic environment. However, more research on the long-term ecological effects of PFOS and PFOA on aquatic fauna are needed to provide important information to adequately assess ecological risk of PFOS and PFOA.     

Investigation of acute toxicity of fenitrothion on guppies Poecilia reticulata

Fenitrothion, an organophosphothionate insecticide (CAS number: 122-14-5) and potential toxic pollutant contaminating aquatic ecosystems, was investigated in the present study for acute toxicity. Guppy fish (Poecilia reticulata) were selected for the bioassay experiments. The experiments were repeated three times and the 96 h LC(50) was determined for the guppies. The static test method of acute toxicity test was used. The water temperature was regulated at 23 +/- 1 degrees C. In addition, behavioral changes at each fenitrothion concentration were observed for the individual fish. Data obtained from the fenitrothion acute toxicity tests were evaluated using the probit analysis statistical method. The 96 h LC(50) value for guppy was estimated as 3.28 mg l(-1). Values in the range of microg l(-1) and mg l(-1) have been reported for various other fish species.     

Toxicity of crude oil and dispersed crude oil to ghost shrimp Palaemon serenus and larvae of Australian bass Macquaria novemaculeata

Acute 96‐h LC50 values of the water‐accommodated fraction (WAF) of crude oil, dispersants (Corexit 9500 and Corexit 9527) and dispersed oil combinations were determined in semistatic bioassays with seawater, using the ghost shrimp Palaemon serenus and larval Australian bass (fish) Macquaria novemaculeata. Sodium dodecyl sulphate (SDS) and zinc sulphate were used as reference toxicants and identical bioassays were conducted using these compounds. Total petroleum hydrocarbon (TPH) uptake of shrimp was also measured on the samples taken from the bioassays. The nominal mean (n=4) 96‐h LC50 standard error (SE) values for WAF of crude oil, Corexit 9527, Corexit 9500, dispersed oil (9527) and dispersed oil (9500) were 258,000 ppm (13,000), 49.4 ppm (6.4), 83.1 ppm (5.8), 8.1 ppm (0.3), and 3.6 ppm (0.3) in the shrimp bioassays, respectively. The nominal mean (n=4) 96‐h LC50 (SE) values calculated from the fish larval bioassays were 465,000 ppm (16,000), 14.3 ppm (0.9), 19.8 ppm (1.6), 28.5 ppm (1.4), and 14.1 ppm (2.6) for WAF of crude oil, Corexit 9527, Corexit 9500, dispersed oil (9527), and dispersed oil (9500), respectively. These LC50 values indicate that dispersed oil combinations were significantly more toxic to these organisms than WAF of crude oil. TPH uptake of shrimp increased in correlation to exposure concentrations, and the presence of dispersant made oil more available for shrimp. © 2000 John Wiley & Sons, Inc. Environ Toxicol 15: 91–98, 2000     

Application of the FETAX protocol to assess the developmental toxicity of nonylphenol ethoxylate to Xenopus laevis and two Australian frogs

The Frog Embryo Teratogenesis Assay-Xenopus (FETAX) protocol has recently been adopted as a valuable tool for evaluating the embryotoxicity of environmental contaminants in amphibians. The bioassay utilises Xenopus laevis as a test species, but there are few comparative studies to evaluate whether data collected in this species is applicable to other amphibians. In this study, the embryotoxicity of the nonionic surfactant, nonylphenol ethoxylate, was determined in X. laevis and the Australian frogs, Litoria adelaidensis and Crinia insignifera using the FETAX protocol. The 96-h LC(50), EC(50) and minimum concentration to inhibit growth (MCIG) values for X. laevis were 3.9-5.4, 2.8-4.6 and 1.0-3.0 mg/l, respectively. The 140-h LC(50), EC(50) and MCIG values for L. adelaidensis were 9.2, 8.8 and 5.1-6.0 mg/l, respectively. The 134-h LC(50), EC(50) and MCIG values for C. insignifera were 6.4, 4.5 and 4.0 mg/l, respectively. Teratogenicity indices for the three species ranged between 1.0 and 1.6, indicating either no or low teratogenicity. Growth inhibition as assessed by embryo length was the most sensitive indicator of effect in all three species. X. laevis was the more sensitive of the three species and the only species that displayed indisputable terata.     

Hazard/Risk Assessment of Pyridaben: I. Aquatic Toxicity and Environmental Chemistry

The toxicity and environmental fate of the insecticide-miticide, pyridaben were investigated using both standardized laboratory procedures and outdoor studies with natural water. Outdoor studies provide a more realistic exposure scenario to aquatic organisms and any toxicity is a response to actual exposure concentrations resulting from the natural degradation and dissipation of the chemical. This paper describes the environmental chemistry/fate and aquatic toxicity of pyridaben. The subsequent paper describes the results of the outdoor aquatic toxicity studies and the use of the water-effect ratio in hazard/risk assessment. Environmental fate studies indicate that pyridaben has a low water solubility and high K_d and K_oc values, which favors partitioning from water onto soil and sediment. Pyridaben is stable to hydrolysis but has a short photolysis half-life in water (<30 min) and soil (11 d). Furthermore, pyridaben has a short half-life in soil (12 to 14 d) when applied in the field to citrus crops. Laboratory studies with constant 48- to 96-h exposures to pyridaben show it is acutely toxic to fish (Lepomis macrochirus, Pimephales promelas, Oncorhynchus mykiss, Cyprinodon variegatus) and invertebrates (Daphnia magna, Mysidopsis bahia). Invertebrates are more sensitive (lower LC50s) than fish to pyridaben, and most mortalities occur <24 h for fish and <72 h for invertebrates. Chronic laboratory studies indicate that the MATCs for pyridaben and D. magna, M. bahia and P. promelas were 0.12, 0.15 and 0.39 g/L, respectively. Acute-to-chronic ratios for pyridaben are low for fish and invertebrates, indicating a low potential for residual activity. Chronic toxicity to aquatic organisms is not an issue after application in the field because exposures tend to be brief.     

Comparing the relative toxicity of malathion and malaoxon in blue catfish Ictalurus furcatus

Malathion inhibits the critical body enzyme, acetylcholinesterase (AChE). This capability requires that malathion should first be converted to malaoxon to become an active anticholinesterase agent. Conversion can be caused by oxidation in mammals, insects, plants, and in sunlight. In this study, the effects of malathion and malaoxon on catfish Ictalurus furcatus were evaluated. After 96-h exposures, the LC(50) (concentration that causes 50% mortality) and IC(50) (concentration that causes 50% enzyme inhibition) for malaoxon were lower than corresponding values for malathion. The overall mean 96-h LC(50) is 17.0 ppm for malathion and 3.1 ppm for malaoxon. IC(50) values for malathion are 8.5 ppm for brain, 10.3 ppm for liver, and 16.6 ppm for muscle. Corresponding values for malaoxon are 2.3, 3.7, and 6.8 ppm, respectively. All the AChE activities in malathion- and malaoxon-exposed catfish brain showed significant inhibition. The oxidation product malaoxon demonstrated higher inhibition on AChE activity than did malathion. Moreover, malaoxon showed significant inhibition on butyrylcholinesterase (BChE) in the liver if the concentrations were increased to more than 1 ppm. Malathion showed no difference between treatment group and control group. Compared with malathion, malaoxon showed higher inhibition on monoamine activity than that of malathion. The results indicated that the oxidative product malaoxon is more toxic than the parent compound malathion. AChE, BChE, and monoamine activities are confirmed as bioindicators of malathion exposure in blue catfish, I. furcatus.     

The toxicity of acetylenic alcohols to the fathead minnow, Pimephales promelas: narcosis and proelectrophile activation

1. The 96-h LC50 values for 16 acetylenic alcohols in the fathead minnow (Pimephales promelas) were determined using continuous-flow diluters. The measured LC50 values for seven tertiary propargylic alcohols agreed closely with the QSAR predictions based upon data for other organic non-electrolytes acting by a narcosis mechanism. 2. Four primary and four secondary propargylic alcohols were 7 to 4600 times more toxic than the respective narcotic toxicity estimated by QSAR. Metabolic activation to electrophilic alpha,beta-unsaturated propargylic aldehydes or ketones is proposed to account for the increased toxicity. 3. 3-Butyn-1-ol and 4-pentyn-2-ol, primary and secondary homopropargylic alcohols, were 320 and 160, respectively, times more toxic than predicted. In this case an activation step involving biotransformation to an allenic electrophile intermediate was proposed.     

Structure-activity relationships for osteolathyrism: II. Effects of alkyl-substituted acid hydrazides

A series of 8 alkyl-substituted acid hydrazides were assayed for their toxicity and teratogenicity using early embryos of the frog Xenopus laevis. Each acid hydrazide was able to induce the connective tissue defect osteolathyrism. The 96-h toxicity (log LC50) and 96-h teratogenicity (log EC50) endpoints are correlated with hydrophobicity measured by the fragment substitution constant (Fr). These relationships suggest the rate limiting step is the ability of the chemical to reach the site of action. However, the teratogenic index (LC50/EC50) is negatively correlated with molar refractivity (MR), a substituent corrected molar volume term. This latter relationship suggests steric hindrance.     

Use of the biotic ligand model to predict pulse-exposure toxicity of copper to fathead minnows (Pimephales promelas)

Concentrations of cationic metals (e.g., Ag, Cd, Cu, Ni, Pb, Zn) and other water quality parameters (e.g., pH, alkalinity, hardness, dissolved organic carbon (DOC) concentration) often cycle daily in surface waters, and the toxicity of the metals to aquatic organisms is altered by variations in those water quality parameters. Consequently, a method is needed to predict the LC50s (median lethal concentrations) of dissolved metals in temporally varying water quality. In this study, we combined the biotic ligand model (BLM), which predicts toxicity of cationic metals across a wide range of water quality conditions, with a one-compartment uptake-depuration (OCUD) model, which predicts toxicity of a chemical at any exposure time in either continuous or time-variable exposures, to test whether we could accurately predict pulse-exposure toxicity of Cu to fathead minnow (FHM; Pimephales promelas) larvae. First, we conducted continuous-exposure toxicity tests to calculate 1- to 96-h Cu LC50s for the FHM larvae. Then we re-parameterized the default Cu BLM for FHM until the corresponding predicted Cu LA50s (medial lethal accumulations at the biotic ligand) collapsed together into a narrow band and also fit the generalized pattern of an OCUD model [i.e., a steeply sloping plot of ln(LA50) versus ln(time) at short exposure times, followed by a gradual approach to an incipient lethal level at longer exposure times]. Next, in 72-h tests, we exposed FHM larvae to 2- or 8-h square-wave pulses of elevated Cu concentration followed by recovery in uncontaminated water for the remaining 22 or 16 h in each of three consecutive 24-h pulse-and-recovery cycles, at pH 6 or 7 in water containing either 0.5 or 2 mEq/L hardness and 0 or 20 mg DOC/L. Using the combined BLM-OCUD model developed from continuous-exposure data, we then predicted the Cu LA50s in the pulse-exposure tests and compared those LA50s to the observed pulse-exposure Cu LA50s. Although predicted pulse-exposure LA50s were within approximately 4x of the observed pulse-exposure LA50s, delayed deaths during the recovery phases of the exposures precluded more accurate predictions of pulse-exposure Cu LA50s and, as a consequence, of pulse-exposure dissolved Cu LC50s. We conclude that one global OCUD equation linked to a re-parameterized Cu BLM for FHM can be used to predict the acute toxicity of continuous and pulse exposures of Cu to FHM larvae across a range of water quality conditions; but to improve the accuracy of those predictions, a mechanism must be developed to account for delayed deaths.     

Estimation of toxicity to marine species with structure-activity models developed to estimate toxicity to freshwater fish

Structure-activity models which were developed to estimate toxicity of chemicals to freshwater fish were tested for use with an estuarine fish (Cyprinodon variegatus) and mysids (Mysidopsis bahia). Significant linear and polynomial relationships that correlated well existed between reported 96-h LC₅₀ values for each marine species and log P (log octanol/water partition coefficient). Good linear relationships were obtained when the 96-h LC₅₀ values for C. variegatus and M. bahia were regressed on water solubility (μmol/l). These models were compared to models developed for freshwater fish using log P and log S. Models using log P to estimate acute toxicity for two freshwater fish produced 96-h LC₅₀ values similar to those measured for C. variegatus and M. bahia, whereas, those models developed with water solubility produced 96-h LC₅₀ values similar to those for C. variegatus, but not for M. bahia. The data indicated that models developed with log P for freshwater fish can be used to estimate toxicity to C. variegatus for a minimum of 58% of the chemicals, whereas models using water solubility estimated toxicity to C. variegatus for a minimum of 77% of the chemicals within an order of magnitude for screening purposes. The calculated 96-h LC₅₀ values were compared to the measured values for each marine species and those measured for Pimephales promelas (fathead minnow) and Poecilia reticulata (guppy). Tests indicated generally that calculated 96-h LC₅₀ values were overestimates of the measured 96-h LC₅₀ values when models for freshwater fish were used to estimate toxicity to each marine species. More data are required for marine species to determine if highly significant relationships between marine and freshwater fish exist with comparisons using larger sample sizes.