Assessment of the effects of chemical mixtures is a very important objective of the ecotoxicological risk assessment. This study was aimed at evaluating for the first time the effects of a mixture of glyphosate and its main breakdown product aminomethylphosphonic acid (AMPA) on various biomarkers in the mussel Mytilus galloprovincialis. Mussels were exposed for 7, 14 and 21 days to either 100 µg/L of glyphosate, 100 µg/L of AMPA or a mixture of both (100 + 100 µg/L). Various haemocyte parameters, such as total haemocyte counts, haemocyte diameter and volume, haemocyte proliferation, haemolymph lactate dehydrogenase activity and haemocyte lysate acid phosphatase activities were measured. In addition, the effects of exposure on the activity of antioxidant enzymes, acetylcholinesterase and glutathione-S-transferase were evaluated in gills and digestive gland from mussels. On the whole, this study demonstrated that the variables considered in the experimental plan, namely treatment, exposure time and their interaction, affect significantly biomarker responses in M. galloprovincialis. The effects of the mixture were comparable to those of the individual compounds, whereas their synergistic effects were occasionally observed, under the experimental conditions tested at least.
Glyphosate is a broad-spectrum, systemic, non-selective, and post-emergence herbicide applied widely as a plant growth regulator. Indeed, glyphosate affects essential aromatic amino acids synthesis in plants, inhibiting protein synthesis1,2. Due to its effectiveness, such compound is an important ingredient of numerous commercial formulations3. After application, a remarkable fraction of glyphosate can deposit directly on the ground, where it can be degraded or leached. Microorganisms can degrade glyphosate to aminomethylphosphonic acid (AMPA) or sarcosine4,5. Consequently, glyphosate and AMPA can be found together in environment.
Regarding aquatic environments, glyphosate and AMPA are detected at measurable concentrations. In USA, the two compounds occurred in various ecosystems with a maximum level of 700 μg/L6. In Argentina, mean concentrations of glyphosate and AMPA of 0.73 μg/L and 0.53 μg/L, respectively, were found in various water bodies7. A recent study demonstrated that the levels of glyphosate and AMPA measured in epilithic biofilms can vary seasonally (from 90 to 305 μg/kg for glyphosate and from 50 to 240 μg/kg for AMPA, in fall and spring, respectively) and suggested that herbicide applications can influence markedly environmental concentrations of the compounds; interestingly, protected sites or with poor access did not show the presence of such contaminants8. Glyphosate has been detected in 39.7% of Italian surface water samples, with 25.2% of cases exceeding 0.1 μg/L, namely the annual environmental quality standard (SQA-MA) for rivers under current legislation9. Regarding seawater, glyphosate (from 28 to 1690 ng/L) and AMPA (from 45 to 4156 ng/L) have been detected in the estuaries of the German coastline. That study demonstrated that glyphosate and AMPA enter the Baltic Sea10. Detectable concentrations of glyphosate (from 13.6 to 1377 µg/L) and AMPA (from 2.58 to 140.8 µg/L) were found in Western Pacific seawater samples11. Mercurio et al.12 recorded half-life values of 47 days for glyphosate in seawater at 25 °C in low-light, of 267 days in the dark at 25 °C and of 315 days in the dark at 31 °C, while AMPA was detected under all conditions. That study demonstrated that glyphosate has a moderate persistence in seawater under low light conditions, but its persistence increases markedly in the dark.
Information available in the literature demonstrate that glyphosate (as active ingredient or commercial formulation) and AMPA affect various biological parameters in non-target aquatic organisms, such as fish13,14, amphibians15, crustacea16,17,18 and molluscs19,20,21,22,23. In two distinct experiments, we have recently demonstrated that exposure to glyphosate (10, 100 and 1000 µg/L) and AMPA (1, 10 and 100 µg/L) affected biomarker responses in Mytilus galloprovincialis24,25, sometimes with similar effects, sometimes with opposing effects.
Most ecotoxicological studies (including ours) have previously been performed to evaluate the effects of individual chemicals on aquatic species. However, aquatic organisms can be exposed to a mixture of different chemicals in the environment. Consequently, in the present study, we evaluated for the first time the impact of a mixture of glyphosate (as active ingredient) and AMPA on various cell and tissue biomarkers of M. galloprovincialis. Considering that i) glyphosate and AMPA can be found together in aquatic environments (including seawater) and that ii) they affect individually biomarker responses in mussels (sometimes with contrasting effects)24,25, we assessed the effects of realistic concentrations (100 µg/L) of glyphosate and AMPA and of a mixture of both (100 + 100 µg/L) to mussels.
Materials and Methods
Specimens of M. galloprovincialis (about 6–7 cm shell length) were sampled in a licensed area for bivalve culture in the Lagoon of Venice (Italy). Before experiments, bivalves were acclimated in the laboratory for one week in large aquaria with aerated seawater (salinity of 35 ± 1, temperature of 18 ± 0.5 °C) and were fed daily ad libitum with microalgae (Isochrysis galbana). Only healthy animals were used for the experiments.
Two separate stock solutions (0.1 g/L, in distilled water) of glyphosate and AMPA (Sigma-Aldrich, Milano, Italy) were prepared, whereas exposure concentrations were obtained by diluting the stock solutions in seawater. Bivalves (seventy per concentration) were exposed for 7, 14 and 21 days to 100 µg/L of glyphosate, 100 µg/L of AMPA and a mixture of 100 µg/L of glyphosate + 100 µg/L of AMPA. Such concentrations were selected on the basis of both information on glyphosate and AMPA levels in aquatic ecosystems reported in Introduction and effects on M. galloprovincialis24,25. Analytical verification of exposure concentrations that were tested in this study has already been performed in our previous studies24,25. Bivalves (thirty-five per tank) were kept in 35 L glass tanks (two per concentration). Seawater, stock and working solutions and microalgae were renewed every two days.
Haemolymph and tissue collection
Haemolymph was sampled from the anterior adductor muscle with a 1-mL plastic syringe and stored at 4 °C in Eppendorf tubes. After 7, 14 and 21 days, pools of haemolymph (5 pools, from 4 bivalves each) from the experimental tanks were prepared. Aliquots of haemolymph were immediately used to measure total haemocyte count (THC), haemocyte diameter and volume, haemocyte proliferation and lactate dehydrogenase (LDH) activity, whereas the remaining aliquots were frozen in liquid nitrogen and stored at −80 °C until analyses. Gills and digestive glands (twenty per concentration) were excised and then pooled (5 pools of 4 mussels each). Subsamples of each pool of tissues were frozen in liquid nitrogen and stored at −80 °C until analyses.
The total haemocyte count (THC), haemocyte diameter and volume were measured using a Scepter™ 2.0 Automated Cell Counter (Millipore, FL, USA). Haemolymph samples (20 µL) were mixed to 2 mL of Coulter Isoton II diluent. THC values were expressed as the number of haemocytes/mL of haemolymph, whereas cell diameter and volume were expressed in µm and picolitres (pL), respectively.
A kit (Cell proliferation Kit II, Roche) was used to evaluate haemocyte proliferation, as described previously26. Absorbance values at 450 nm were recorded with a Beckman 730 spectrophotometer. The results were expressed as optical density OD450/mL of haemolymph.
Another kit (Cytotoxicity Detection Kit, Roche) was used to measure lactate dehydrogenase activity (LDH) in cell-free haemolymph (CFH). To obtain CFH, haemolymph samples (500 µL) were centrifuged at 780 × g for 10 min, and supernatant (=CFH) was then collected for the assay following the manufacturer’s instructions. The results were expressed as OD490/mL haemolymph.
The Acid Phosphatase Assay kit (Sigma-Aldrich, Milano, Italy) was used to measure acid phosphatase activity in haemocyte lysate (HL) according to the manufacturer’s instructions. To obtain HL, haemolymph samples were centrifuged at 780 × g for 10 min, and haemocytes were resuspended in distilled water, mixed for 15 sec using a vortex mixer and centrifuged at 10,000 × g for 10 min. The supernatant (=HL), was removed for the acid phosphatase assay. The results were expressed as U/mg protein. Protein concentrations in HL were quantified according to Bradford27.
Tissue preparation and enzyme activity measurement
Gills and digestive gland samples were homogenised on ice with an Polytron homogeniser (PT 1200 E) in five volumes of 10 mM Tris-HCl buffer, pH 7.5, containing 0.15 M KCl, 0.5 M sucrose, 1 mM EDTA and protease inhibitor cocktail (Sigma-Aldrich), and centrifuged at 12,000 g for 45 min at 4 °C. Supernatants (SN) were used for analyses.
SOD activity was measured in triplicate using the xanthine oxidase/cytochrome c method28. Results were expressed as U/mg protein; one unit of SOD being defined as the amount of sample causing 50% inhibition under the assay conditions. SN protein concentrations were quantified according to Bradford27.
CAT activity was determined in triplicate following the method of Aebi29. Results were expressed as U/mg protein; one unit of CAT is defined as the amount of enzyme that catalysed the dismutation of 1 μmol of H2O2/min. SN protein concentrations were also measured27.
Gill acetylcholinesterase (AChE) activity was measured following the method of Ellman et al.30. The results were expressed as nmol/min/mg of protein. The protein concentration in SN was quantified according to Bradford27.
Glutathione S-transferase (GST) activity was measured in digestive gland SN according to the method described in Habig et al.31 and results were expressed as nmol/min/mg protein.
The normal distribution of data (Shapiro-Wilk’s test) and the homogeneity of the variances (Bartlett’s test) were assessed. The whole data set (“all parameters” in Table 1) was statistically analysed using the Permutational multivariate Analyses of Variance (PERMANOVA, with 9999 permutations), in order to detect significant effects of treatment, exposure time and the interaction between treatment and time. The variables “treatment”, “exposure time” and their interaction were considered as fixed factors. Data from each biomarker were also analysed with PERMANOVA to determine significant effects of the variables considered on haemocytes/haemolymph and soft tissues parameters. In addition, the non-parametric post hoc test (Mann-Whitney U test) was used for pairwise comparisons of results from control and treated groups at each sampling time. All results were expressed as the mean ± standard deviation (SD). The software packages Statistica 13.4 (TIBCO Software Inc.) and PRIMER 6 PERMANOVA Plus (PRIMER-E Ltd, Plymouth, UK) were used for the statistical analyses. Lastly, a canonical correlation analysis (CCA) was performed, including exposure concentrations, exposure duration, and the measured cellular and biochemical parameters as variables. The software package R32 with the CCA package33 were used.
Statistical analysis indicated that the three variables of the experimental plan (treatment, exposure time and treatment*time interaction) had significant effects on all the biological parameters measured in mussels (Table 1). Regarding the results of post-hoc test at each tissue sampling time, asterisks in the figures denote the significant differences in biomarker responses that were due to the variables “treatment” and “treatment*time interaction” between control and exposed mussels.
The variables “exposure time” and “treatment*time interaction” significantly (p < 0.001) influenced haemocyte parameters. In particular, exposure time affected significantly all the haemocyte parameters measured, whereas the variable “treatment*time interaction” influenced significantly THC (p < 0.01), cell proliferation (p < 0.01) and LDH activity (p < 0.01) (Table 1). Regarding pairwise comparisons, THC was shown to decrease significantly in mussels exposed for 7 days to glyphosate (p < 0.05), AMPA (p < 0.05) and the mixture (p < 0.001), whereas a significant (p < 0.05) increase in THC was recorded in mussels exposed for 14 days to the mixture (Fig. 1A).
Haemocyte proliferation resulted influenced significantly by both the variables “exposure time” (p < 0.05) and “treatment*time interaction” (p < 0.01) (Table 1). As for pairwise comparisons, haemocyte proliferation was shown to increase significantly in animals exposed for 7 days to glyphosate (p < 0.05) and the mixture (p < 0.01), in those treated for 14 days with AMPA (p < 0.05), and decreased significantly (p < 0.05) in mussels exposed for 21 days to the mixture, in comparison with controls (Fig. 1D).
Like haemocyte proliferation, LDH activity was affected significantly by “exposure time” (p < 0.001) and “treatment*time interaction” (p < 0.01) (Table 1). In particular, the exposure for 21 days to the mixture enhanced significantly (p < 0.01) LDH activity, compared to control group (Fig. 1E).
Although acid phosphatase activity increased in HL of mussels exposed for 7 days to both AMPA and the mixture, and decreased in those treated for 14 and 21 days, pairwise comparisons did not reveal significant differences compared with the controls (Fig. 1F).
Gill and digestive gland enzyme activities
Considering all the parameters measured in soft tissues, namely gills and digestive gland, PERMANOVA analysis indicated that the variables “treatment” and “exposure time” affected significantly (p < 0.05 and p < 0.001, respectively) enzyme activities (Table 1).
Considering separately the results obtained in the two tissues, PERMANOVA analysis revealed significant effects of the variables “exposure time” (p < 0.001) and “treatment*time interaction” (p < 0.05) on gill biomarkers (Table 1). PERMANOVA analysis performed on individual biomarker results demonstrated no significant variations of SOD activity (Table 1; Fig. 2A), whereas a significant (p < 0.001) time-dependent effect on CAT and AChE activities was observed (Table 1; Fig. 2B,C). In addition, AChE resulted significantly (p < 0.05) influenced by “treatment*time interaction” variable (Table 1). As for pairwise comparisons, AChE activity was shown to decrease significantly (p < 0.05) in bivalves treated for 7 days with AMPA and the mixture, increased (p < 0.05) in those exposed for 14 days at the same experimental conditions, and decreased again (p < 0.05) in mussels exposed for 21 days to the three experimental concentrations tested, with respect to controls (Fig. 2C).
As for digestive gland parameters, a significant (p < 0.05) effect of the variable “treatment” (Table 1) was recorded. The three variables considered did not affect SOD activity during the study (Table 1; Fig. 2D). Conversely, “treatment” significantly (p < 0.01) affected CAT activity (Table 1; Fig. 2E), whereas “exposure time” influenced significantly (p < 0.01) GST activity (Table 1; Fig. 2F). In detail, a statistically significant (p < 0.05) decrease of CAT activity was observed in mussels exposed for 7 and 21 days to the mixture, whereas CAT activity increased significantly (p < 0.05) in those treated for 14 days with AMPA, compared to the related controls (Fig. 2E).
A plot of the first two components of the CCA analysis are depicted in the biplot in Fig. 3. The first principal correlations are 92% and 87% for the first and the second canonical correlation, respectively. The samples highlighted a marked influence of the experimental plan on the biomarkers. Moreover, a clear time-dependent pattern of variation can be highlighted, Time 1 (= 7 days, in the bottom part) being clearly separated from Times 2–3 (= 14 and 21 days, respectively; in the upper part). Samples from dose = 0 are well separated from other doses, especially at Time 7. Dose “0” and dose “GLY + AMPA” (= mixture) show the largest distance in all the times (most pronounced at Time 7).
In the current ecotoxicological studies it is crucial to evaluate the effects of contaminant mixtures in order to highlight the risk posed by differing substances occurring simultaneously in the environment34. In this study, a suite of biomarkers was measured in differing tissues from mussels to assess the impact of environmentally relevant concentrations of glyphosate and AMPA, alone or as a mixture.
At the cellular level, our study demonstrated that glyphosate and AMPA (alone or in combination) affected THC values in mussels, even if with a different pattern of variation between 7 (decreasing trend) and 14 days (increasing trend) of exposure. Significant decreases in THC values were previously recorded in M. galloprovincialis exposed in two distinct experiments for 7 and 14 days to glyphosate24 and for 21 days to AMPA25. Interestingly, in the present study despite a different pattern of variation in THC values was recorded in bivalves treated for 7 and 14 days, it can be highlighted that exposure to the mixture of glyphosate and AMPA exacerbated the effects of the individual compounds. In addition, results obtained suggested that mussels exposed for 14 days were trying to compensate the initial (7 days) drastic reduction in THC, mainly in bivalves exposed to the mixture. It is commonly assumed that THC increases owing to either cell proliferation or mobilisation of haemocytes from peripheral tissues into the haemolymph, whereas THC decrease owing to cell death or the enhanced movement of haemocytes from the haemolymph into tissues35,36. In our study, no significant correlation between THC and haemocyte proliferation (Pearson’s correlation coefficient r = −0.11, p = 0.367) was recorded. Therefore, we speculated that the reduction recorded in bivalves following 7 days of exposure to all the experimental conditions tested was caused by increased haemocyte mobilisation from haemolymph into the peripheral tissues. Alternatively, it can be hypothesised that the significant increase in cell proliferation recorded in mussels exposed for 7 days was due to a strategy of animals to compensate - partially at least - the reduction in the number of circulating haemocytes. As for available data on the effects of glyphosate and AMPA on this important cell parameters, a recent study demonstrated significant reductions in THC values in the freshwater shrimp, Macrobrachium nipponensis, exposed for 24 h to 1.40, 2.80 and 5.60 mg/L glyphosate, and for 96 h to 5.60 mg/L16. In the crab Eriocheir sinensis, THC decreased significantly after 6 h of exposure to all glyphosate concentrations tested (4.4 to 98 mg/L), with highest reduction of 42.21% at 98 mg/L17. Conversely, 7 days of exposure to 10 mg/L of Roundup® (= 48% of glyphosate) increased significantly THC in the snail Biomphalaria alexandrina, both in Schistosoma mansoni-infected animals and healthy snails37. Overall, this study suggested that the mixture of glyphosate and AMPA affected markedly THC values in M. galloprovincialis, even if the pattern of variation of THC was different between mussels treated for 7 days and those treated for 74 days.
In this study, although slight increases in both diameter and volume of haemocytes were generally recorded in M. galloprovincialis, differences were not significant with respect the related controls. Similarly, no significant changes in haemocyte size were found in Crassostrea gigas following exposure to the pesticide metaldehyde38. Conversely, in our previous survey, glyphosate increased significantly cell volume in haemocytes from M. galloprovincialis exposed for 7 days to 1000 µg/L and 21 days to 10 µg/L24. As for AMPA, our previous study demonstrated that haemocyte diameter decreased significantly in bivalves treated for 14 days with 100 µg/L, whereas haemocyte volume was shown to increase significantly in animals exposed for 14 days to 1 and 10 µg/L of AMPA and decreased significantly at 100 µg/L, with respect to controls25. Results of our study suggested that the mixture of glyphosate and AMPA did not influence haemocyte size in M. galloprovincialis.
As stated above, in the present study haemocyte proliferation increased significantly in animals exposed for 7 days to both glyphosate and mixture, and in those treated for 14 days with AMPA. Conversely, cell proliferation decreased significantly in bivalves treated for 21 days with the mixture. We have previously demonstrated that exposure of M. galloprovincialis to the highest concentration of AMPA induced a significant increase in haemocyte proliferation throughout the study25. However, in this study no correlation between haemocyte proliferation and THC values was recorded. Consequently, we speculated that haemocyte proliferation increased in treated mussels to compensate - at least partially - for the reduction in THC, as already suggested for AMPA-exposed mussels25. Unfortunately, no further information about the effects of glyphosate and AMPA (alone or as a mixture) on cell proliferation is available in the literature, to the best of our knowledge at least.
LDH is a cytoplasmic enzyme that can be released into the extracellular fluids by damaged cells. Consequently, LDH assay can be used to detect signs of cell membrane destabilisation. Our study indicated that exposure to the mixture increased significantly LDH activity in CFH of mussels exposed for 21 days, suggesting a reduction in haemocyte membrane stability. In our previous studies, exposure to glyphosate was shown to increase significantly LDH activity in CFH from mussels exposed for 7 (at 10 and 1000 µg/L) and 14 days (at 10 µg/L)24, whereas exposure to AMPA increased significantly LDH activity in animals treated for 14 with 100 µg/L and for 21 days with the three concentrations tested25. Destabilisation of cell membrane was also recorded in other mollusc species exposed to Roundup®39, to the herbicides fomesafen40 and atrazine41. Overall, this study suggested that haemocyte membrane stability can be affected by the mixture of glyphosate and AMPA, similarly to what was observed previously by testing individual compounds.
Regarding lysosomal hydrolytic enzymes, this study demonstrated that exposure of mussels to the compounds tested did not alter significantly acid phosphatase activity. Non-linear results have previously been obtained after exposure of M. galloprovincialis to glyphosate alone, acid phosphatase activity decreasing significantly in HL of animals treated for 7 days with 1000 µg/L and for 21 days with 100 and 1000 µg/L, and increasing after exposure for 14 days to 1000 µg/L24. Following treatment of the crab Eriocheir sinensis with glyphosate, acid phosphatase activity was shown to decrease markedly in CFH from animals exposed for 6 h to 96 h to relatively high concentrations of the contaminant (e.g., 44 and 98 mg/L)17. On the basis of the results of this study, we can state that acid phosphatase is not a target of the mixture of glyphosate and AMPA.
Gill and digestive gland enzyme activities
Of the enzyme activities measured in M. galloprovincialis, only gill AChE and digestive gland CAT resulted influenced significantly by the variables “treatment” and “treatment*time interaction”, respectively. Regarding antioxidant enzymes, exposure to the mixture of glyphosate and AMPA was shown to decrease CAT activity, in particular in digestive gland of mussels treated for 7 and 21 days. Conversely, a significant reduction in soft tissue SOD activity (but not in CAT activity) was observed in the golden mussel L. fortunei following exposure for 26 days to glyphosate (1, 3 and 6 mg/L)42. In a recent study conducted by the same authors on the same mussel species demonstrated that glyphosate did not affect significantly SOD and CAT activities after 28 days of dietary exposure with the microalgae Scenedesmus vacuolatus previously treated with a commercial formulation of glyphosate (6 mg/L, as active principle)22. The authors suggested that differences in the results of the two studies22,42 could be due to exposure modality of mussels (glyphosate dose and availability in experiments with treated microalgae could be lower than those in waterborne exposure). In the clam Corbicula fluminea, exposure for 96 h to 2 and 10 mg/L of Roundup® caused a significant increase in SOD activity in gills and a significant decrease in CAT activity of digestive gland from animals treated with the highest concentration tested21. In the freshwater shrimp M. nipponensis, SOD and CAT activities and total antioxidant capacity was shown to decrease in a dose- and time-dependent manner in serum of animals exposed for 96 h to high concentrations (0.70, 1.40, 2.80 and 5.60 mg/L) of Roundup®16. Overall, the results obtained in this study suggested that exposure to the mixture of glyphosate and AMPA affects antioxidant enzyme activity in M. galloprovincialis, as for digestive gland and CAT activity at least.
AChE activity measurement is a useful biomarker to assess the effects of neurotoxic compounds - organophosphate compounds in particular - in marine organisms43,44. Results obtained in this study demonstrated that the exposure to both AMPA and the mixture (and to glyphosate at 21 days) affected significantly AChE activity in mussels. Interestingly, a biphasic response of animals to the contaminants was recorded: AChE activity decreased after 7 days of exposure to AMPA and the mixture, increased after 14 days at the same experimental conditions, and decreased again after 21 days at all the doses tested. It can be hypothesised that AChE activity increased in 14 days-exposed mussels to balance the initial reduction recorded at 7 days, whereas enzyme inhibition recorded after 21 days suggested inability of mussels to counteract exposure effects. In M. nipponensis, exposure to Roundup® decreased significantly AChE activity in serum of shrimps exposed for 24 h to 96 h16. In an in vitro study, glyphosate (0.075 to 15 mM) was shown to inhibit cholinesterase activity in gills and muscle from the mussel Perna perna and in brain and muscle from the fish Danio rerio and Jenynsia multidentata45. Conversely, no significant alterations in AChE activity were recorded in L. fortunei following direct exposure to glyphosate42 or via glyphosate-contaminated food (microalgae)22. Overall, results of our study suggested that the mixture of glyphosate and AMPA affected significantly AChE activity in mussels.
GST is involved in phase II of xenobiotic detoxification process46. The resulting products are more hydrophilic and more easily excreted47. Generally, increased GST activity indicates high capability of tissues/cells to remove xenobiotics. In the present study, no significant variations in GST activity were observed in digestive gland of bivalves exposed to glyphosate, AMPA and their mixture. Similarly, no significant alterations in GST activity were found in gills and digestive gland of C. fluminea following exposure for 96 h to 2 and 10 mg/L of Roundup®21. Conversely, a significant increase (72%) in the GST activity was observed in L. fortunei fed for 28 days with the glyphosate-treated microalgae Scenedesmus vacuolatus22. The exposure for 42 days to the glyphosate-containing formulation Roundup Max® (0.2 and 2 mg/L) induced a significant decrease in GST activity in the liver of the fish Cnesterodon decemmaculatus, whereas no significant changes were recorded in brain, gills and muscle48.
Summarising, our study demonstrated that exposure to a mixture of realistic doses of glyphosate and AMPA influences cell and tissue biomarkers in the mussel M. galloprovincialis. In particular, inhibition of AChE activity in mussel gills is noteworthy. Although further studies are necessary to elucidate better the mode of action of the contaminants tested (alone or in combination), results reported here suggest a potential ecotoxicological risk for bivalve molluscs.
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This research was supported by the University of Padova, Project PRID-Seed “Ecotoxicological risk assessment for the herbicide glyphosate and its main degradation product, aminomethylphosphonic acid, in bivalves”.
The authors declare no competing interests.
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Matozzo, V., Munari, M., Masiero, L. et al. Ecotoxicological hazard of a mixture of glyphosate and aminomethylphosphonic acid to the mussel Mytilus galloprovincialis (Lamarck 1819). Sci Rep 9, 14302 (2019). https://doi.org/10.1038/s41598-019-50607-0
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