Scholarly article on topic ' Effects of Glyphosate and its Formulation, Roundup, on Reproduction in Zebrafish ( Danio rerio ) '

Effects of Glyphosate and its Formulation, Roundup, on Reproduction in Zebrafish ( Danio rerio ) Academic research paper on "Environmental engineering"

0
0
Share paper
Academic journal
Environmental Science & Technology
OECD Field of science

Academic research paper on topic " Effects of Glyphosate and its Formulation, Roundup, on Reproduction in Zebrafish ( Danio rerio ) "

fpOHl

Science sTecnno ogy

Subscriber access provided by DUESSELDORF LIBRARIES

Article

Effects of glyphosate and its formulation, Roundup, on reproduction in zebrafish (Danio rerio).

Tamsyn M Uren Webster, Lauren V Laing, Hannah Florance, and Eduarda M. Santos Environ. Sci. Technol., Just Accepted Manuscript • Publication Date (Web): 23 Dec 2013 Downloaded from http://pubs.acs.org on December 30, 2013

Just Accepted

"Just Accepted" manuscripts have been peer-reviewed and accepted for publication. They are posted online prior to technical editing, formatting for publication and author proofing. The American Chemical Society provides "Just Accepted" as a free service to the research community to expedite the dissemination of scientific material as soon as possible after acceptance. "Just Accepted" manuscripts appear in full in PDF format accompanied by an HTML abstract. "Just Accepted" manuscripts have been fully peer reviewed, but should not be considered the official version of record. They are accessible to all readers and citable by the Digital Object Identifier (DOI®). "Just Accepted" is an optional service offered to authors. Therefore, the "Just Accepted" Web site may not include all articles that will be published in the journal. After a manuscript is technically edited and formatted, it will be removed from the "Just Accepted" Web site and published as an ASAP article. Note that technical editing may introduce minor changes to the manuscript text and/or graphics which could affect content, and all legal disclaimers and ethical guidelines that apply to the journal pertain. ACS cannot be held responsible for errors or consequences arising from the use of information contained in these "Just Accepted" manuscripts.

Environmental Science & Technology is published by the American Chemical Society. 1155 Sixteenth Street N.W., Washington, DC 20036

Published by American Chemical Society. Copyright © American Chemical Society. However, no copyright claim is made to original U.S. Government works, or works produced by employees of any Commonwealth realm Crown government in the course of their duties.

1 Effects of glyphosate and its formulation,

2 Roundup®, on reproduction in zebrafish (Danio

3 rerio).

4 Tamsyn. M. Uren Webster1*, Lauren V. Laing1, Hannah Florance1 and Eduarda M. Santos1*

5 1. Biosciences, College of Life & Environmental Sciences, Geoffrey Pope Building, University

6 of Exeter, Exeter, EX4 4QD

7 * Corresponding authors

8 9 10 11 12

16 ABSTRACT

17 Roundup®, and its active ingredient glyphosate, are among the most widely used herbicides

18 worldwide, and may contaminate surface waters. Research suggests both Roundup® and

19 glyphosate induce oxidative stress in fish, and may also cause reproductive toxicity in

20 mammalian systems. We aimed to investigate the reproductive effects of Roundup® and

21 glyphosate in fish, and the potential associated mechanisms of toxicity. To do this, we conducted

22 a 21-day exposure of breeding zebrafish (Danio rerio) to 0.01, 0.5 and 10 mg/L (glyphosate acid

23 equivalent) Roundup® and 10 mg/L glyphosate. 10 mg/L glyphosate reduced egg production, but

24 not fertilisation rate in breeding colonies. Both 10 mg/L Roundup® and glyphosate increased

25 early-stage embryo mortalities and premature hatching. However, exposure during

26 embryogenesis alone did not increase embryo mortality, suggesting that this effect was caused

27 primarily by exposure during gametogenesis. Transcript profiling of the gonads revealed 10

28 mg/L Roundup® and glyphosate induced changes in the expression of cyp19a1 and esrl in the

29 ovary, and hsd3b2, cat and sodl in the testis. Our results demonstrate that these chemicals cause

30 reproductive toxicity in zebrafish, although only at high concentrations unlikely to occur in the

31 environment, and likely mechanisms of toxicity include disruption of the steroidogenic

32 biosynthesis pathway and oxidative stress.

39 INTRODUCTION

41 Glyphosate is extensively used worldwide, topping lists of agricultural herbicide usage in

42 Europe [1] and the US [2]. It is a broad-spectrum, post emergence herbicide, which acts by

43 binding phosphoenolpyruvate, the substrate of EPSP synthase, and subsequently inhibiting

44 aromatic amino acid synthesis via the shikimate pathway in plants [3, 4]. Glyphosate is generally

45 applied as part of a formulated product, the most widely used of which are the Roundup®

46 herbicides. Roundup® formulations contain glyphosate in the form of an isoproylamine salt,

47 which aids solubility but does not affect its properties as the active ingredient, together with

48 various adjuvants which enhance its herbicidal properties. One of the most important and

49 commonly used adjuvants is polyethoxylated tallow amine (POEA), a surfactant that enhances

50 penetration of glyphosate through the plant cuticle [5, 6]. Glyphosate and Roundup® are also

51 extensively used as domestic and urban-area weed-killers [2]. Commercial glyphosate

52 formulations vary in composition with country and purpose and the properties of these

53 formulations, including their toxicity, can be compared using the concentration of glyphosate

54 present, expressed as glyphosate acid equivalent (a.e.).

55 Glyphosate is known to strongly adsorp to soil, where it is subject to microbial degradation.

56 This is one of glyphosate's advantageous herbicidal properties, limiting agricultural input to

57 surface waters in ideal conditions. However, pulses of contamination can be expected when

58 rainfall occurs directly after application and when flood events increase river sediment load [6].

59 Urban runoff and wastewater treatment effluent also account for considerable glyphosate input

60 into rivers [7]. Despite its widespread use, concentrations of glyphosate, or its associated

61 formulation components, are not routinely monitored in surface waters. However, glyphosate

concentrations worldwide have been regularly reported to occur up to ~10-15 |ig/L in rivers [e.g.8, 9]. Considerably higher peaks in concentration, in the high |ig/L range, have also been measured, but are mainly associated with direct aquatic application, and in isolated wetland environments [6, 10].

Although the target mechanism of action of glyphosate and glyphosate-based formulations is specific to plants, they have been shown to induce diverse biological effects in a range of nontarget organisms. In fish, much of previous research assessing effects of Roundup® and glyphosate has focused on their induction of oxidative stress through ROS generation and/or interference with cellular antioxidant production. Short-term exposures (up to 6 days) to 1-20 mg/L of several Roundup® formulations in a number of fish species altered levels of cellular antioxidants and induced oxidative damage of DNA, lipids and proteins [e.g. 11, 12-15]. Environmentally relevant concentrations of Roundup®, glyphosate and POEA have also induced DNA damage in blood and liver cells of eel and catfish after up to 9 days exposure [16-19]. Other studies have found that Roundup®, and in some cases glyphosate, induce other effects in fish including neurotoxicity and immunotoxicity [e.g. 20, 21, 22]. Similar evidence of Roundup® and glyphosate toxicity has been found for other vertebrate species, and demonstrated effects include occurrence of developmental abnormalities, especially in amphibians [23, 24]. Roundup® formulations have largely been found to be more toxic than pure glyphosate. The inherent toxicity of POEA [17, 23], and potentially other formulation components, is likely to contribute to this, although a modulating effect on glyphosate toxicity is also possible. Few studies, however, have directly compared equivalent concentrations of Roundup® and glyphosate.

The potential of Roundup® to disrupt the endocrine system in vitro has been demonstrated in mammalian cell lines. In mouse Leydig cells, sub-lethal concentrations of Roundup® (from 25

85 mg/L) altered the transcription and activity of steroidogenic acute regulatory protein (StAR),

86 resulting in disruption of progesterone production [25]. A number of studies demonstrated

87 consistent inhibition of aromatase activity by Roundup® in various human cell lines. The

88 concentrations required to cause these effects varied depending on the cell type and formulation,

89 but included from 4 mg/L in liver cells and 72 mg/L in placental and embryonic cells [26-28].

90 Less consistently, and to a smaller extent than Roundup®, aromatase inhibition by glyphosate

91 alone has also been reported (approximately 10 fold higher concentrations) [28]. Additionally,

92 both glyphosate and Roundup® were reported to reduce testosterone production in rat testicular

93 cells at concentrations from 0.36 mg/L [29], but it is difficult to relate these results to the

94 potential effects of these chemicals in vivo. Few studies have investigated the effects of

95 glyphosate and its commercial formulations on the endocrine system in vivo. Drakes treated with

96 5 and 100 mg Roundup®/kg (body weight) exhibited reduced levels of testosterone,

97 corresponding with alterations in testis structure. In rats, maternal and juvenile treatment from 5

98 and 50 mg/kg (body weight) of Roundup® impaired male reproductive development, with effects

99 including alteration in testis structure, sperm production and sex steroid production [30-32].

100 Reproductive effects of Roundup® and glyphosate in fish have seldom been investigated and

101 are far from clear. While no evidence of altered gonadal development was evident in juvenile

102 stickleback exposed to 0.1-100 |ig/L glyphosate [33], treatment with 3.6 mg/L Roundup® had

103 some negative impact on offspring production in Silver catfish [34]. The mechanisms

104 contributing to this reproductive effect have not been investigated.

105 Given the extensive usage of glyphosate based herbicides, there is a clear potential for the

106 environmental exposure of fish populations to glyphosate together with associated formulation

107 products, which may modify its toxicity. This study aimed to examine the effects of Roundup®

formulation on reproduction in fish and to determine to what extend these effects were associated with the toxicity of glyphosate alone. To do this, we conducted a 21 day reproductive test in breeding colonies of zebrafish, to determine if reproduction, embryo development and embryo survival, were affected by exposure to 0.01, 0.5 and 10 mg/L (glyphosate acid equivalent) Roundup® and 10 mg/L glyphosate. The two lower Roundup® concentrations included in this study were chosen to represent concentrations that can be expected to occur in the environment regularly (0.01 mg/L) and during occasional peak contamination events (0.5 mg/L). The highest concentration tested (10 mg/L) is unlikely to occur in surface waters, and was included to facilitate the analysis of the mechanisms of toxicity. We included a treatment group exposed to 10 mg/L glyphosate alone to allow for a direct comparison of its mechanisms of toxicity with the equivalent a.e. concentration of Roundup®. We hypothesised that the mechanisms of toxicity resulting in effects on reproduction might include oxidative stress and disruption of steroid biosynthesis, and to investigate this we conducted transcript profiling of a suite of genes involved in these processes in the gonads.

MATERIALS AND METHODS

Fish maintenance

Colonies of 4 male and 4 female adult (20 week old) WIK strain zebrafish were established in individual 15 L glass tanks and allowed to breed naturally during a 7 day acclimation period. Fish were maintained according to Paull et al. [35] and a full description of husbandry procedures is provided in the supporting information.

131 Chemical exposures

132 Chemical exposure was conducted via a flow through system for a period of 21 days in

133 accordance with OECD guidelines for fish reproductive tests, preceded by a 10 day pre-exposure

134 period [36]. The treatment groups consisted of three concentrations of Roundup®; 0.01, 0.5 and

135 10 mg/L glyphosate acid equivalent (using Roundup® GC liquid glyphosate concentrate

136 containing 120 g/L glyphosate acid; Monsanto, Cambridge, UK); 10 mg/L glyphosate (analytical

137 grade; Molekula, Wimborne, UK); and a control group. Each treatment group was comprised of

138 three replicate breeding colonies (4 males and 4 females) in 15L tanks. Water samples were

139 collected from each tank on days 7, 14 and 21 of the exposure period and stored at -20 °C prior

140 to chemical analysis. Details of the analytical chemistry procedures are provided in supplemental

141 material.

143 Reproductive test and embryo exposures

144 Group spawning occurred daily at dawn and eggs were collected 1 hour post fertilisation (hpf),

145 rinsed thoroughly to remove detritus and incubated in water containing the same chemical

146 exposure concentrations as their tank of origin, at 28 °C. Exposure water for the embryo

147 experiments was made according to the ISO 7346-3:1996 guidelines [37], fully oxygenated and

148 supplemented with 2.5 |il/L of the antifungal agent Methylene Blue (Interpet; Dorking, UK) to

149 avoid mortalities caused by fungal infections. The eggs from each colony were examined using

150 light microscopy between 2 ^ and 3 ^ hours after dawn, when all fertilised eggs had reached at

151 least the 16-cell stage during early cleavage [38], and the total number of fertilised and

152 unfertilised eggs were quantified on each day throughout the pre-exposure and exposure periods.

153 During the 21-day chemical exposure, fertilised eggs displaying cellular necrosis were counted

and recorded as early-stage mortalities (<3.5 hpf). Fifty fertilised eggs from each tank were selected randomly and incubated in 50 ml exposure water until 72 hpf. During this period, embryo mortality was recorded at 24, 54 and 72hpf and embryo hatching was recorded at 54 and 72 hpf.

In order to determine if the observed effects of Roundup® and glyphosate on embryos were due to the effects of exposure during gametogenesis or during embryogenesis, embryos collected from a control population were exposed to a range of concentrations of glyphosate and Roundup® as above. Chemical treatment was initiated between 10-20 minutes post fertilisation. In addition to the exposure concentrations used for the adult exposures, embryos were also treated with higher concentrations (50, 100, 250, 500 and 1000 mg/L a.e. Roundup® and glyphosate) to determine the concentration thresholds for embryo mortalities and developmental toxicity. Experiments were conducted in triplicate; each replicate contained 50 embryos and observations of mortalities and hatching were performed as described above.

Sampling

All fish were humanely sacrificed on day 21 of the exposure period by a lethal dose of benzocaine (0.5 g L-1; Sigma-Aldrich) followed by destruction of the brain, in accordance with UK Home Office regulations. Wet weight and fork length were recorded and the condition factor (k= (weight (g) x 100)/ (fork length (cm))) was calculated for individual fish. Livers were dissected and weighed, and the hepatosomatic index (HSI) (liver weight (mg)/ total weight (mg)) x 100)) was determined for individual fish. Gonads were dissected, weighed and one gonad from each fish was snap frozen in liquid nitrogen and stored at -80°C prior to transcript profiling. The remaining gonad was fixed in Bouin's solution (Sigma-Aldrich) for histological analysis. The

177 gonadosomatic index (GSI; gonad weight (mg)/ total weight (mg)) x 100)) was determined for

178 both males and females.

180 Transcript profiling and histological analysis

181 Transcript profiling of genes encoding steroidogenic enzymes, sex steroid receptors and

182 antioxidant enzymes, was conducted using RT-QPCR in the gonads of exposed fish according to

183 [39]. Histological analysis of the gonads was conducted according to [40]. A full description of

184 these methodologies is presented in the supporting information.

186 Statistical analysis

187 Statistical analyses were conducted with SigmaStat (version 12.0). Before analysis,

188 proportional data (embryo survival and hatching) were subjected to variance-stabilising square-

189 root or arcsine transformations as appropriate. All reproductive output and sampling data met

190 assumptions of normality and equal variance. Outliers in transcript expression data were

191 identified and removed according to Chauvenet's criterion [41] prior to statistical analysis.

192 Transcript expression data that did not meet normally-distributed criteria was log transformed

193 before statistical analysis. All data was analysed using single factor one way analysis of variance

194 (ANOVA), followed by the Holm-Sidak post hoc test using a pairwise comparison method. Data

195 were considered to be significant when P < 0.05.

197 RESULTS

199 Water chemistry

The mean measured concentrations of glyphosate in the tank water were between 88-140 % of the nominal values for all treatments (quantification of glyphosate in tanks receiving 0.01 mg/L Roundup® was below the detection limit of our method), and are presented in Table S2.

Morphometric parameters

The mean mass and length of male and female fish were 375.0 ± 6.3 mg/ 32.6 ± 0.2 mm and 402.6 ± 9.3 mg/ 31.7 ± 0.2 mm respectively. There were no significant differences in size or condition factor (mean 1.08 and 1.25 for males and females, respectively) between treatment groups. Additionally, we observed no alteration of general health or behaviour in any colony. The GSI of females was significantly lower in the fish treated with 10 mg/L glyphosate compared to the control group (Figure 1c). There was no significant difference in the GSI of males between treatment groups, or in the HSI of males or females.

Reproductive test and embryo exposures

During the 10 day pre-exposure period, there was no difference in cumulative egg production between the treatment groups (P=0.468). During the exposure period, colonies in the control group consistently spawned the greatest number of eggs per female, while those treated with 10 mg/L glyphosate spawned the least. From day 10 of the exposure period, cumulative egg production was significantly reduced in colonies exposed to 10 mg/L glyphosate compared to the controls, and this difference intensified throughout the remainder of the exposure period. At the end of the 21 day exposure, cumulative egg production was significantly lower in colonies exposed to 10 mg/L glyphosate compared to the control, and also compared to the 10 and 0.01 mg/L Roundup® groups (Figure 1a,b). Additionally, egg output significantly correlated (R2=

223 0.79; P= 0.043) with female GSI across all treatment groups. Fertilisation rate remained

224 consistently high throughout the exposure period with no significant differences between

225 treatment groups and an overall mean value of 83.4%.

226 There was a significant increase in embryo mortalities occurring before 3.5 hpf in embryos

227 from both the 10 mg/L Roundup® and glyphosate treatment groups (Figure 2a). Additionally,

228 there was a significant correlation between early embryo mortality and the concentration of

229 Roundup® (R2= 0.52; P=0.008). There were no significant differences between treatments in

230 embryo mortality between the start of epiboly (3.5 hpf) and the end of somitogenesis at 24 hpf

231 (Figure 2b). However, there was a significant increase in the percentage of embryos that had

232 hatched at 54 hpf in groups treated with 10 mg/L Roundup® and 10 mg/L glyphosate compared

233 to the control group (Figure 2b).

234 For embryos originating from a control population, exposure to glyphosate and Roundup® at

235 the concentrations used in the adult reproductive test (0, 0.01, 0.5 and 10 mg/L Roundup® and 10

236 mg/L glyphosate) did not result in increased mortality rate at either 3.5 hpf or 24 hpf (Figure

237 2a,b), but there was a significant increase in 3.5-24 hpf mortality in embryos exposed to

238 concentrations >100 mg/L glyphosate and > 500 mg/L Roundup® (Figure S4a). We also

239 observed evidence of developmental delay and abnormalities from concentrations > 50 mg/L

240 glyphosate and >250 mg/L Roundup® at 24 hpf. There was a trend towards increased hatching at

241 54 hpf in groups exposed to 10 and 50 mg/L Roundup® and glyphosate, and there was a

242 significant correlation between hatching rate at 54hpf and exposure concentration of Roundup®

243 up to 50 mg/L (R2= 0.27; P=0.04) (Figure S4b). For embryos exposed to > 100 mg/L Roundup®

244 and glyphosate, we found evidence of progressive delay in development and hatching with

245 increasing concentration.

Gonad transcript profiling

In the ovary, the transcript encoding aromatase (cyp19a1) was significantly up-regulated in the 10 mg/L Roundup® treatment group compared to the controls. Estrogen receptor 1 (esr1) in the 10 mg/L Roundup® group was significantly up-regulated compared to the 10 mg/L glyphosate group. There were similar, but not statistically significant, decreasing trends in expression of other steroidogenic enzymes including cytochrome P450, subfamilies 17 and 11 (cyp17a1, cyp11a1) and 3P-hydroxysteroid dehydrogenase (hsd3b2) in groups exposed to both Roundup® and glyphosate. In contrast, for the antioxidants glutathione peroxidase (gpx1a), catalase (cat) and glutathione-S-transferase pi (gstp1) non-significant, increasing trends in transcript expression were observed (Figure 3 a, Figure S1a).

In the testis, hsd3b2 was significantly up-regulated following exposure to 10 mg Roundup®/L compared to all other treatment groups. The expression pattern of steroidogenic acute regulatory protein (star), cyp17a1, cyp11a1 and the androgen receptor (ar) additionally appeared to follow an expression pattern similar to hsd3b2 across treatment groups. cat was significantly up-regulated in groups exposed to both 10 mg/L Roundup® and 10 mg/L glyphosate compared to those treated with 0.5 mg/L Roundup®. In addition, sod1 was significantly up-regulated in the 10 mg/L compared to 0.5 mg/L Roundup® groups (Figure 3b, Figure S1b).

Gonad Histology

Histological examination of females from all treatment groups showed that the ovaries of all individuals contained oocytes at all stages of development (oogonia, primary oocytes, cortical alveoli stage oocytes, secondary oocytes and mature vitellogenic oocytes) and the majority

269 contained recent post-ovulatory follicles. We found evidence of ovarian abnormalities in 9.1,

270 18.2, 9.1, 50.0 and 63.6 % of females in the control, 0.01 mg/L Roundup®, 0.5 mg/L Roundup®,

271 10 mg/L Roundup® and 10 mg/L glyphosate treatment groups, respectively (Figure S3). The

272 majority of abnormalities were relatively mild and included accumulation of eosinophilic fluid

273 and presence of abnormal tissue. In addition, the proportion of fish containing atretic oocytes in

274 their ovaries also appeared to be increased (Figure S2).

275 Histological examination of males showed that testes of all individuals from all treatment

276 groups contained germ cells at all stages of spermatogenesis (including spermatogonia,

277 spermatocytes, spermatids and mature spermatozoa) (Figure S2). There were no abnormalities

278 and no differences between stages of development between treatment groups.

280 DISCUSSION

282 Reproductive effects on adult zebrafish

283 This study provides evidence that glyphosate caused a reduction in the number of eggs

284 spawned by female zebrafish exposed to high concentrations (10 mg/L) of glyphosate. However,

285 this concentration is well above concentrations measured to date in the environment and unlikely

286 to occur in aquatic systems, except when glyphosate is directly applied to control algal

287 populations. In addition, our study also showed an apparent reduction, albeit not significant, in

288 egg production in all three Roundup® treated groups. Therefore, the potential for adverse effects

289 of Roundup® on reproductive output and impact on wild populations cannot be ruled out. A

290 number of potential mechanisms may contribute to the observed effect of glyphosate on egg

291 production, including disruption of normal progression through oogenesis, inhibition of

ovulation and increased rate of oocyte atresia. In order to explore this, we conducted histological analysis of the gonads of exposed females and observed a trend towards an increase in the incidence of ovarian abnormalities as a result of exposure to both Roundup® and glyphosate. Ovarian follicle atresia is an apoptotic process leading to re-absorption of maturing oocytes rather than ovulation. It is a highly-regulated, natural process thought to have a role in maintaining ovarian homeostasis; however various environmental stressors, as well as disruption of the hormonal control of oogenesis and ovulation, have been shown to increase atresia [42]. We found atretic vitellogenic oocytes in all treatment groups, but this incidence tended to increase in both the 10 mg/L Roundup® and 10 mg/L glyphosate treatment groups. Similarly, in these groups we also found an increased trend in the incidence of abnormal ovarian tissue, including excess connective tissue and putative haemopoietic tissue. In some females treated with 0.01 and 10 mg/L Roundup® and 10 mg/L glyphosate we observed the presence of areas containing eosinophilic fluid. Previously, accumulated proteinaceous fluid in the ovary has been found to contain vitellogenin, and this has been associated with a disruption in the endocrine control of oogenesis in zebrafish through exposure to elevated levels of 17P-oestradiol [43].

It is important to note that despite the trends towards increased incidence of atretic follicles and ovarian abnormalities following exposure to glyphosate and Roundup®, the majority of fish were only moderately affected and their ovaries contained oocytes at all stages of maturation, including mature vitellogenic oocytes and post-ovulatory follicles. Moreover, we found no differences in the ovarian expression of bcl2-associated X protein (baxa) and tumour protein 53 (tp53), which are typical marker genes of apoptosis. This indicates that oocyte atresia was unlikely to be the major mechanism responsible for the decline in egg production rate induced by glyphosate treatment. Corresponding with this, a similar degree of atresia in fish exposed to

315 Roundup® was not accompanied by a significant decline in egg-production in this treatment

316 group. Therefore, we hypothesise that the observed decrease in egg production following

317 exposure to glyphosate was more likely to be due to a reduction in the number of follicles

318 undergoing oogenesis. The strong correlation between egg production and female GSI, including

319 a significant reduction in GSI in females exposed to 10 mg/L glyphosate, which indicates

320 reduced gonadal volume, provides support for this hypothesis.

321 Sex steroids are essential for the regulation of oogenesis, and alterations in sex steroid

322 biosynthesis may have contributed to the reduction of egg production in colonies exposed to

323 glyphosate. To test this hypothesis, we investigated the effects of glyphosate and Roundup® on

324 the expression of a number of transcripts encoding enzymes involved in steroid biosynthesis,

325 several of which have previously been shown to be targets of their toxicity [25-28]. We found a

326 significant increase in the expression of ovarian aromatase, an enzyme which catalyses the

327 conversion of testosterone to oestradiol in granulosa cells, in the gonads of females exposed to

328 10 mg/L Roundup®, and also an increasing trend in those exposed to 10 mg/L glyphosate.

329 Several previous studies have demonstrated that Roundup® disrupts both aromatase activity and

330 cyp19a1 expression levels in a number of human cell lines, and there is some evidence that

331 glyphosate can also inhibit aromatase activity, especially with the addition of small percentages

332 of Roundup®, which may facilitate its cellular entry [26-28]. Romano et al. [32] proposed

333 inhibition of aromatase as a causative mechanism for disruption of steroidogenesis and adverse

334 reproductive impacts in the male offspring of rats exposed to Roundup® during pregnancy. The

335 stimulatory effect of Roundup® on cyp19a1 expression observed in the present study contrasts

336 with the predominantly inhibitory effects found in the in vitro studies. This may reflect the

337 complex nature of feedback mechanisms governing steroid biosynthesis pathways in vivo or,

possibly, a compensatory transcriptional response to a potential inhibition of aromatase enzyme. Additionally, it is difficult to equate the concentrations used in the present study with those used in the in vitro studies. It is possible that differential stimulatory and inhibitory responses occur with concentration, and also with time. Although not significant, there were also similar decreasing trends in expression of steroidogenic enzymes, hsd3b2, cyp17a1 and cypllal, in females treated with both 10 mg/L of Roundup® and 10 mg/L glyphosate, indicating a possible wider effect on steroidogenic pathways.

The differential regulation of ovarian esrl by Roundup® and glyphosate is interesting and may reflect the effect of other chemicals present in Roundup® formulation on this receptor. Increased esrl expression following Roundup® exposure may have resulted from compensatory mechanisms in the ovary to maintain or restore oestrogen signalling pathways. This may explain, at least in part, the differences in the effects of these chemicals on egg production, with glyphosate having a more pronounced effect than Roundup®. Using human liver HepG2 cells, Gasnier [26] showed that Roundup® and glyphosate antagonistically bind oestrogen receptors (ERa and ERfi), although Kojima [44] found no evidence of agonistic or antagonistic interaction with oestrogen receptors in Chinese hamster ovary cells. A recent study showed glyphosate actively bound oestrogen receptors and induced proliferative growth of oestrogen-dependent breast cancer cells, and also increased protein levels of ERa and ERp [45]. Taken together, our ovarian transcript profiling data suggests that Roundup® and glyphosate may have disrupted steroid hormone biosynthesis and also potentially modulated the biological effects of oestrogens via alterations in the expression of esrl, the predominant oestrogen receptor in the ovary.

Despite having no significant effect on egg production, it is interesting to note that exposure to 10 mg/L Roundup® also elicited alterations in gene expression often in the opposite direction of

361 those induced by exposure to the equivalent concentration of glyphosate alone. This might

362 suggest the presence of compensatory mechanisms ameliorating the adverse effects of

363 glyphosate when in the presence of the other constituents of Roundup®. A possible mechanism

364 could be increased synthesis of aromatase to maintain sex steroid ratios and oestrogen signalling

365 in the ovary in order to promote oogenesis, and maintain egg production.

366 There was no effect of exposure to Roundup® or glyphosate on fertilisation rate.

367 Corresponding with this, histological examination revealed no evidence of any disruption of

368 spermatogenesis, or abnormalities in the testis following exposure to glyphosate or Roundup®.

369 Therefore, we found no indication that these chemicals affect the ability of the sperm produced

370 to fertilise eggs. This contrasts with several previous in vivo studies that have found some

371 evidence that Roundup® disrupts spermatogenesis in rats, resulting in testis pathology, sperm

372 abnormalities and altered sperm production [30-32]. It is important to note, however, that our

373 experimental conditions are optimised to maximise reproduction and may not detect subtle

374 changes in sperm quality that may be sufficient to cause effects under the conditions found in the

375 natural environment.

376 Previous Roundup®-induced testicular toxicity has been associated with alterations in

377 steroidogenesis and sex steroid levels in rats and drakes [30-32, 46]. In the current study,

378 analysis of transcripts encoding steroidogenic enzymes in the testes showed that hsd3b2 was

379 significantly up-regulated in males exposed to 10 mg/L Roundup® compared to those exposed to

380 0.01 and 0.5 mg/L Roundup®, and 10 mg/L glyphosate (Figure 3b). Moreover, although not

381 statistically significant, the expression patterns of the other steroidogenic enzymes profiled (star,

382 cyp17a1 and cypllal), as well as ar, followed a similar expression pattern to hsd3b2 across

383 treatment groups. This pattern, of apparent down-regulation in the 0.5 mg/L Roundup® treatment

and up-regulation in the 10 mg/L Roundup® group was robust across tank replicates. Walsh et al. [25] found evidence that Roundup®, but not glyphosate, disrupted StAR and P450scc (Cyp11a1) in mouse testis cells, primarily through alteration of protein expression and activity, suggesting that such post-transcriptional regulatory changes should also not be ruled out. Additionally, we found 10 mg/L Roundup® significantly increased expression cat and sodl compared to the lower Roundup® treatments, and 10 mg/L glyphosate also significantly increased cat expression in the testis. Together, these changes in the transcription of antioxidant enzymes provide evidence that both Roundup® and glyphosate induce oxidative stress in the testis. Therefore, despite no apparent impacts on fertilisation success, we have found some evidence that high concentrations of Roundup® and glyphosate cause disruption of steroidogenesis and oxidative stress in the testis, suggesting that their potential to cause adverse impacts on male reproductive health should not be ruled out. It is interesting to note that exposure to 10 mg/L Roundup® elicited differential responses, in terms of the magnitude and direction of transcript expression changes, compared to 10 mg/L glyphosate, possibly suggesting greater compensatory mechanisms of response following exposure to Roundup®, similarly to that observed in females.

Effects on embryo survival and development

We found evidence that treatment with both 10 mg/L Roundup® and glyphosate induce an increased rate of embryo mortality during very early development. We observed necrosis of the fertilised embryos during cleavage and early blastula stages, prior to progression to epibioly at ~3.5 hpf (as described by Kimmel et al. [38]). In order to assess if the early stage mortality was caused as a direct result of the chemical exposure on embryos or by the parental exposure, we exposed embryos originating from a control population of untreated adults and found that

407 concentrations of up to 10 mg/L of Roundup® and 10 mg/L glyphosate had no effect on embryo

408 survival at <3.5 or 3.5-24 hpf. This corresponds with previous work showing exposure of

409 zebrafish embryos to up to 10 mg/L glyphosate for 5 days had no effect on survival or

410 development [47]. We only found a significant increase in embryo mortality at concentrations of

411 100 mg/L glyphosate and 1000 mg/L Roundup®, which are 10 and 1000 times higher than the

412 concentrations used in the reproductive study. Moreover, this mortality predominantly occurred

413 between 3.5-24 hpf, rather than in the earlier stages of development. These high concentrations

414 of glyphosate, and to a lesser extent Roundup® formulation, result in a pronounced decrease in

415 pH in the exposure water (to 3.8 (100 mg/L glyphosate) and 4.9 (1000 mg/L Roundup®)), which

416 may be responsible for the embryo toxicity seen. Overall, these results suggest that the increase

417 in early stage mortalities observed in embryos originating from fish exposed to 10mg/L

418 Roundup® and glyphosate is attributable to potential damage of the gametes occurring during

419 gametogenesis and/or fertilisation, rather than as a result of direct embryo exposure.

420 Alternatively, it is possible that maternal transfer of glyphosate, Roundup® or formulation

421 products, via the yolk, might contribute to embryo exposure to these toxicants and the increased

422 mortality observed.

423 As discussed above, gonadal transcript profiling revealed significant up-regulation of

424 transcripts encoding antioxidant enzymes in response to exposure to 10 mg/L Roundup® and 10

425 mg/L glyphosate in the testes and increasing trends in transcripts encoding antioxidant enzymes

426 in the ovary. Oxidative stress induced in the testis by chemical exposure has been shown to cause

427 DNA damage in developing sperm [48]. Pérez-Cerezales et al. [49] showed that DNA damage in

428 rainbow trout sperm did not impair fertilisation success, but resulted in a high rate of embryo

429 mortality in early stages of embryogenesis, particularly during gastrulation. This is consistent

with our findings that fertilisation success was unaffected, but that an increased rate of embryo mortalities occurred during early stages of development and before transition to epiboly. Therefore, we hypothesise that oxidative stress generation in the testis during spermatogenesis is likely to be an important causative mechanism responsible for the increase in early-stage embryo mortality. Additionally, the increase in ovarian histological abnormalities and the increased trends in ovarian antioxidant transcript expression suggest similar damage during oogenesis is also possible, although oocytes are thought to have greater response and repair mechanisms to counter-act oxidative stress than sperm [49, 50]. DNA damage after spermiation cannot be ruled out, but probably has a minimal effect compared to damage during spermatogenesis, given the brief period of less than 65 seconds that sperm remains motile before fertilisation (Van Look et al., personal communication).

We found an increased percentage of hatching at 54 hpf in groups exposed to 10 mg/L Roundup® and 10 mg/L glyphosate. Additionally, embryos originating from the unexposed control population showed a significant increasing trend in hatching rate at 54 hpf with concentrations up to 50 mg/L Roundup®, as well as an apparent increase in hatching in those treated with 10 mg/L glyphosate. This suggests an independent impact of Roundup® and glyphosate on embryos, not entirely attributable to toxicity during gametogenesis. Hatching is variable, and dependent on a number of environmental factors. Various chemical and other environmental stressors, such as temperature, are known to affect developmental rate and, subsequently, time to hatch. However, in this study, observations at 24h, 48h, 54 and 72 hpf showed no obvious change in development rate between treatment groups, indicating that exposure to 10 mg/L Roundup® and 10 mg/L glyphosate induces premature hatching in zebrafish. At 72 hpf, more than 90 % of embryos from all treatment groups had hatched (both

453 those originating from exposed and non-exposed adults), and there were no obvious behavioural

454 or morphological differences between treatments. In natural populations, premature hatching

455 could potentially result in detrimental impacts for population sustainability, for example by

456 increasing the susceptibility to predation.

457 We found no obvious signs of developmental toxicity at exposure concentrations up to 10

458 mg/L Roundup® or glyphosate, which corresponds with the findings of Stehr [47]. We did find

459 evidence of developmental delay in embryos exposed to concentrations > 50 mg/L glyphosate

460 and >250 mg/L Roundup® and hypothesise that the increased toxicity of glyphosate may be

461 attributed to its greater acidity than the buffered Roundup® formulation. With the exception of

462 amphibians, which appear particularly sensitive [e.g. 23, 24], these results show that only

463 extremely high concentrations of Roundup® and glyphosate induce developmental toxicity in

464 zebrafish and are generally in accordance with evidence from other species, including rats [51]

465 and sea urchins [52].

466 Overall, we have found evidence that both 10 mg/L Roundup® and 10 mg/L glyphosate have

467 similar adverse impacts on embryo survival and hatching, while 10 mg/L glyphosate reduces egg

468 production. We have found some evidence that these reproductive effects occur via multiple

469 mechanisms of toxicity which appear to differ, to some extent, between Roundup® and its active

470 ingredient glyphosate. These mechanisms may include disruption of the steroidogenic pathway

471 and sex steroid signalling, and generation of oxidative stress. This work demonstrates that both

472 glyphosate and Roundup® have a detrimental impact on a number of measures of reproductive

473 health in zebrafish, although only at very high concentrations that are unlikely to occur in the

474 environment, based on the currently available measurements. Given the growing concern over

475 potential reproductive effects of these compounds, and their extremely widespread usage, this

provides valuable mechanistic information for their environmental risk assessment, particularly when considering the potential effects of complex mixtures of environmental contaminants.

495 FIGURES

496 Figure 1. (A) Cumulative egg production during the 10 day pre-exposure and 21 day chemical

497 exposure periods (n=3 replicate colonies per treatment); (B) Mean number of eggs laid per

498 female per day throughout the 21 day exposure period (n=3 replicate colonies per treatment); and

499 (C) Mean gonad-somatic index of females in each treatment group (n=12 individual females per

500 treatment). Data plotted are mean values ± SEM. Asterisks indicate significant differences

501 between treatment groups (*P<0.05 **P<0.01 ***P<0.001).

Figure 2. Effects of Roundup® and glyphosate on embryo survival and development. Black bars represent embryos originating from exposed parental populations (n= 3 replicate colonies, for each colony data was collected every day for 21 days of exposure and averaged) and grey bars represent embryos originating from a control parental population (n=3 replicate exposures, each replicate containing 50 embryos). (A) Percentage of embryo mortalities that occurred before 3.5 hpf; (B) percentage of embryo mortalities that occurred between 3.5-24 hpf; and (C) percentage of embryos that had hatched at 54 hpf in each treatment group. Data plotted are mean values ± SEM. Asterisks represent significant differences from the control treatment (***P<0.001).

516 Figure 3. Transcript profiling of target genes in the ovary (A) and testis (B) following

517 exposure to Roundup® (R) and glyphosate (G). Data are presented as fold change relative to

518 expression in the control group, whereby red shading indicates up-regulation and green shading

519 represents down-regulation. Relative expression was calculated as ratio of target gene /rpl8

520 mRNA concentration. For each treatment, n= 6-8 fish. Individual data points classified as

521 outliers, and for which the expression was below the detection limit of the assay were excluded

522 from the analysis. Lettering indicates significant differences between treatment group, with

523 groups identified with different letters being significantly different from each other (P< 0.05).

ASSOCIATED CONTENT Supporting Information contains: Page S2: Supplemental Experimental Section

Page S4: Target genes, primer sequences and assay details for RT-QPCR analysis, Table S1.

Page S5: Measured concentrations of glyphosate in tank water, Table S2.

Page S6: Transcript profiling of target genes in the gonads, Figure S1.

Page S7: Gonad histology of control and exposed fish, Figure S2.

Page S8: Occurrence of ovarian histological abnormalities, Figure S3.

Page S9: Effects of glyphosate and Roundup® on embryos originating from a control population, Figure S4.

This material is available free of charge via the Internet at http://pubs.acs.org.

552 AUTHOR INFORMATION

553 Corresponding Authors

554 * Tamsyn M. Uren Webster

555 Biosciences, College of Life & Environmental Sciences, Geoffrey Pope Building, University of

556 Exeter, Exeter, EX4 4QD

557 tu202@exeter.ac.uk

558 Phone: +44 (0)1392 724677

559 Fax: +44 (0)1392 263434

561 * Eduarda M. Santos

562 Biosciences, College of Life & Environmental Sciences, Geoffrey Pope Building, University of

563 Exeter, Exeter, EX4 4QD

564 E.Santos@exeter.ac.uk

565 Phone: +44 (0)1392 264607

566 Fax: +44 (0)1392 263434

568 ACKNOWLEDGMENTS

569 We wish to thank Dr James Cresswell for advice on the statistical analysis and Dr Gregory

570 Paull for help with the fish husbandry and experimental design. This work was funded by a

571 Natural Environment Research Council CASE PhD studentship (Grant number NE/I528326/1)

572 and the Salmon & Trout Association.

574 REFERENCES

575 1. European Commission, The use of plant protection products in the European Union.

576 Eurostat 2007.

577 2. US EPA, Pesticides Industry Sales and Usage: 2006 and 2007 Market Estimates. 2011.

578 3. Schonbrunn, E.; Eschenburg, S.; Shuttleworth, W. A.; Schloss, J. V.; Amrhein, N.;

579 Evans, J. N. S.; Kabsch, W., Interaction of the herbicide glyphosate with its target enzyme 5580 enolpyruvylshikimate 3-phosphate synthase in atomic detail. Proceedings of the National

581 Academy of Sciences 2001, 98, (4), 1376-1380.

582 4. Steinrucken, H. C.; Amrhein, N., The herbicide glyphosate is a potent inhibitor of 5583 enolpyruvylshikimic acid-3-phosphate synthase. Biochemical and Biophysical Research

584 Communications 1980, 94, (4), 1207-1212.

585 5. Brausch, J. M.; Smith, P. N., Toxicity of three polyethoxylated tallowamine surfactant

586 formulations to laboratory and field collected fairy shrimp, Thamnocephalus platyurus. Archives

587 of Environmental Contamination and Toxicology 2007, 52, (2), 217-221.

588 6. Giesy, J. P.; Dobson, S.; Solomon, K. R., Ecotoxicological risk assessment for

589 Roundup® herbicide. Reviews of environmental contamination and toxicology 2000, 167, 35590 120.

591 7. Botta, F.; Lavison, G. l.; Couturier, G.; Alliot, F.; Moreau-Guigon, E.; Fauchon, N.;

592 Guery, B. n. d.; Chevreuil, M.; Blanchoud, H. l. n., Transfer of glyphosate and its degradate

593 AMPA to surface waters through urban sewerage systems. Chemosphere 2009, 77, (1), 133-139.

594 8. Byer, J. D.; Struger, J.; Klawunn, P.; Todd, A.; Sverko, E., Low cost monitoring of

595 glyphosate in surface waters using the ELISA method: An evaluation. Environmental Science &

596 Technology 2008, 42, (16), 6052-6057.

597 9. Struger, J.; Thompson, D.; Staznik, B.; Martin, P.; McDaniel, T.; Marvin, C., Occurrence

598 of glyphosate in surface waters of southern Ontario. Bulletin of Environmental Contamination

599 and Toxicology 2008, 80, (4), 378-384.

600 10. Battaglin, W. A.; Rice, K. C.; Focazio, M. J.; Salmons, S.; Barry, R. X., The occurrence

601 of glyphosate, atrazine, and other pesticides in vernal pools and adjacent streams in Washington,

602 DC, Maryland, Iowa, and Wyoming, 2005-2006. Environ. Monit. Assess. 2009, 155, (1), 281603 307.

604 11. Cavalcante, D.; Martinez, C.; Sofia, S., Genotoxic effects of Roundup® on the fish

605 Prochilodus lineatus. Mutation Research/Genetic Toxicology and Environmental Mutagenesis

606 2008, 655, (1), 41-46.

607 12. Modesto, K. A.; Martinez, C. u. B., Roundup causes oxidative stress in liver and inhibits

608 acetylcholinesterase in muscle and brain of the fish Prochilodus lineatus. Chemosphere 2010, 78,

609 (3), 294-299.

610 13. Cavas, T.; Konen, S., Detection of cytogenetic and DNA damage in peripheral

611 erythrocytes of goldfish (Carassius auratus) exposed to a glyphosate formulation using the

612 micronucleus test and the comet assay. Mutagenesis 2007, 22, (4), 263-268.

613 14. Lushchak, O. V.; Kubrak, O. I.; Storey, J. M.; Storey, K. B.; Lushchak, V. I., Low toxic

614 herbicide Roundup induces mild oxidative stress in goldfish tissues. Chemosphere 2009, 76, (7),

615 932-937.

616 15. Ferreira, D.; Costa da Motta, A.; Kreutz, L. C.; Toni, C.; Loro, V.; Barcellos, L.,

617 Assessment of oxidative stress in Rhamdia quelen exposed to agrichemicals. Chemosphere 2010,

618 79, (9), 914-921.

619 16. Guilherme, S.; Gaivao, I.; Santos, M.; Pacheco, M., European eel (Anguilla anguilla)

620 genotoxic and pro-oxidant responses following short-term exposure to Roundup®, a glyphosate-

621 based herbicide. Mutagenesis 2010, 25, (5), 523-530.

622 17. Guilherme, S.; Santos, M.; Barroso, C.; Gaivao, I.; Pacheco, M., Differential genotoxicity

623 of Roundup® formulation and its constituents in blood cells of fish (Anguilla anguilla):

624 considerations on chemical interactions and DNA damaging mechanisms. Ecotoxicology 2012,

625 1-10.

626 18. Guilherme, S.; Gaivao, I.; Santos, M.; Pacheco, M., DNA damage in fish (Anguilla

627 anguilla) exposed to a glyphosate-based herbicide "Elucidation of organ-specificity and the role

628 of oxidative stress. Mutation Research/Genetic Toxicology and Environmental Mutagenesis

629 2012.

630 19. de Castilhos Ghisi, N.; Cestari, M. M., Genotoxic effects of the herbicide Roundup in the

631 fish Corydoras paleatus (Jenyns 1842) after short-term, environmentally low concentration

632 exposure. Environ. Monit. Assess. 2013, 185, (4), 1-7.

633 20. Glusczak, L.; Miron, D. d. S.; Moraes, B. S.; Simaues, R. l. R.; Schetinger, M. R. C.;

634 Morsch, V. M.; Loro, V. n. L., Acute effects of glyphosate herbicide on metabolic and enzymatic

635 parameters of silver catfish Rhamdia quelen. Comparative Biochemistry and Physiology Part C:

636 Toxicology & Pharmacology 2007, 146, (4), 519-524.

637 21. Kreutz, L. C.; Gil Barcellos, L. J.; de Faria Valle, S.; de Oliveira Silva, T. l.; Anziliero,

638 D.; Davi dos Santos, E.; Pivato, M.; Zanatta, R., Altered hematological and immunological

639 parameters in silver catfish Rhamdia quelen following short term exposure to sublethal

640 concentration of glyphosate. Fish & Shellfish Immunology 2011, 30, (1), 51-57.

641 22. Kelly, D. W.; Poulin, R.; Tompkins, D. M.; Townsend, C. R., Synergistic effects of

642 glyphosate formulation and parasite infection on fish malformations and survival. Journal of

643 Applied Ecology 2010, 47, (2), 498-504.

644 23. Howe, C. M.; Berrill, M.; Pauli, B. D.; Helbing, C. C.; Werry, K.; Veldhoen, N., Toxicity

645 of glyphosate based pesticides to four North American frog species. Environmental Toxicology

646 and Chemistry 2004, 23, (8), 1928-1938.

647 24. Relyea, R. A., New effects of Roundup on amphibians: Predators reduce herbicide

648 mortality; herbicides induce antipredator morphology. Ecol. Appl. 2012, 22, (2), 634-647.

649 25. Walsh, L. P.; McCormick, C.; Martin, C.; Stocco, D. M., Roundup inhibits

650 steroidogenesis by disrupting steroidogenic acute regulatory (StAR) protein expression.

651 Environmental Health Perspectives 2000, 108, (8), 769.

652 26. Gasnier, C.; Dumont, C.; Benachour, N.; Clair, E.; Chagnon, M. C.; Seralini, G. E.,

653 Glyphosate-based herbicides are toxic and endocrine disruptors in human cell lines. Toxicology

654 2009, 262, 184-191.

655 27. Richard, S.; Moslemi, S.; Sipahutar, H.; Benachour, N.; Seralini, G.-E., Differential

656 effects of glyphosate and roundup on human placental cells and aromatase. Environmental

657 Health Perspectives 2005, 113, (6), 716.

658 28. Benachour, N.; Sipahutar, H.; Moslemi, S.; Gasnier, C.; Travert, C.; Seralini, G., Time-

659 and dose-dependent effects of roundup on human embryonic and placental cells. Archives of

660 Environmental Contamination and Toxicology 2007, 53, (1), 126-133.

661 29. Clair, A.; Mesnage, R.; Travert, C.; Seralini, G. E., A glyphosate-based herbicide induces

662 necrosis and apoptosis in mature rat testicular cells in vitro, and testosterone decrease at lower

663 levels. Toxicology in Vitro 2012, 26, (2), 269-279.

664 30. Romano, R. M.; Romano, M. A.; Bernardi, M. M.; Furtado, P. V.; Oliveira, C. A.,

665 Prepubertal exposure to commercial formulation of the herbicide glyphosate alters testosterone

666 levels and testicular morphology. Archives of Toxicology 2010, 84, 309-317.

667 31. Dallegrave, E.; Mantese, F. D.; Oliveira, R. T.; Andrade, A. J.; Dalsenter, P. R.;

668 Langeloh, A., Pre-and postnatal toxicity of the commercial glyphosate formulation in Wistar rats.

669 Archives of Toxicology 2007, 81, (9), 665-673.

670 32. Romano, M. A.; Romano, R. M.; Santos, L. D.; Wisniewski, P.; Campos, D. A.; de

671 Souza, P. B.; Viau, P.; Bernardi, M. M.; Nunes, M. T.; de Oliveira, C. A., Glyphosate impairs

672 male offspring reproductive development by disrupting gonadotropin expression. Archives of

673 Toxicology 2012, 86, (4), 663-673.

674 33. Le Mer, C.; Roy, R. L.; Pellerin, J.; Couillard, C. M.; Maltais, D., Effects of chronic

675 exposures to the herbicides atrazine and glyphosate to larvae of the threespine stickleback

676 (Gasterosteus aculeatus). Ecotoxicology and Environmental Safety 2013.

677 34. Soso, A. B.; Barcellos, L. J. G.; Ranzani-Paiva, M. J.; Kreutz, L. C.; Quevedo, R. M.;

678 Anziliero, D.; Lima, M.; Silva, L. B. d.; Ritter, F.; Bedin, A. C., Chronic exposure to sub-lethal

679 concentration of a glyphosate-based herbicide alters hormone profiles and affects reproduction of

680 female Jundia (Rhamdia quelen). Environmental Toxicology and Pharmacology 2007, 23, (3),

681 308-313.

682 35. Paull, G. C.; Van Look, K. J. W.; Santos, E. M.; Filby, A. L.; Gray, D. M.; Nash, J. P.;

683 Tyler, C. R., Variability in measures of reproductive success in laboratory-kept colonies of

684 zebrafish and implications for studies addressing population-level effects of environmental

685 chemicals. Aquat. Toxicol. 2008, 87, 115-126.

686 36. OECD, OECD Guideline for the Testing of Chemicals: Fish Short Term Reproductive

687 Assay. 2009.

688 37. ISO Water Quality, Determination of the Acute Lethal Toxicity of Substances to a

689 Freshwater Fish [Brachydanio rerio Hamilton-Buchanan (Teleostei, cyprinidae)], Part 3. Flow-

690 Through Method; International Organization for Standardization. 1996.

691 38. Kimmel, C. B.; Ballard, W. W.; Kimmel, S. R.; Ullmann, B.; Schilling, T. F., Stages of

692 embryonic development of the zebrafish. Developmental Dynamics 1995, 203, (3), 253-310.

693 39. Uren-Webster, T. M.; Lewis, C.; Filby, A. L.; Pauli, G. C.; Santos, E. M., Mechanisms of

694 toxicity of di(2-ethylhexyl) phthalate on the reproductive health of male zebrafish. Aquatic

695 Toxicology 2010, 99, 360-369.

696 40. Santos, E. M.; Workman, V. L.; Paull, G. C.; Filby, A. L.; Van Look, K. J. W.; Killie, P.;

697 Tyler, C. R., Molecular basis of sex and reproductive status in breeding zebrafish. Physiol.

698 Genomics 2007, 30, 111-122.

699 41. Chauvenet, W., A manual of spherical and practical astronomy. Lippincott: Philadelphia,

700 1863.

701 42. Lubzens, E.; Young, G.; Bobe, J.; Cerda , J., Oogenesis in teleosts: how fish eggs are

702 formed. General and Comparative Endocrinology 2010, 165, (3), 367-389.

703 43. van der Ven, L. T. M.; Wester, P. W.; Vos, J. G., Histopathology as a tool for the

704 evaluation of endocrine disruption in zebrafish (Danio rerio). Environmental Toxicology and

705 Chemistry 2003, 22, (4), 908-913.

706 44. Kojima, H.; Katsura, E.; Takeuchi, S.; Niiyama, K.; Kobayashi, K., Screening for

707 estrogen and androgen receptor activities in 200 pesticides by in vitro reporter gene assays using

708 Chinese hamster ovary cells. Environmental Health Perspectives 2004, 112, (5), 524.

709 45. Thongprakaisang, S.; Thiantanawat, A.; Rangkadilok, N.; Suriyo, T.; Satayavivad, J.,

710 Glyphosate induces human breast cancer cells growth via estrogen receptors. Food Chem.

711 Toxicol. 2013, 59, 129-136.

712 46. Oliveira, A. G.; Telles, L. F.; Hess, R. A.; Mahecha, G. n. A.; Oliveira, C. A., Effects of

713 the herbicide Roundup on the epididymal region of drakes Anas platyrhynchos. Reproductive

714 Toxicology 2007, 23, (2), 182-191.

715 47. Stehr, C. M.; Linbo, T. L.; Baldwin, D. H.; Scholz, N. L.; Incardona, J. P., Evaluating the

716 effects of forestry herbicides on fish development using rapid phenotypic screens. North

717 American Journal of Fisheries Management 2009, 29, (4), 975-984.

718 48. Lewis, C.; Galloway, T., Reproductive consequences of paternal genotoxin exposure in

719 marine invertebrates. Environmental Science & Technology 2009, 43, (3), 928-933.

720 49. Perez-Cerezales, S.; Martinez-Paramo, S.; Beirao, J.; Herraez, M., Fertilization capacity

721 with rainbow trout DNA-damaged sperm and embryo developmental success. Reproduction

722 2010, 139, (6), 989-997.

723 50. Menezo, Y.; Dale, B.; Cohen, M., DNA damage and repair in human oocytes and

724 embryos: a review. Zygote 2010, 18, (4), 357-365.

725 51. Dallegrave, E.; Mantese, F. D.; Coelho, R. S.; Pereira, J. n. D.; Dalsenter, P. R.;

726 Langeloh, A., The teratogenic potential of the herbicide glyphosate-Roundup® in Wistar rats.

727 Toxicology Letters 2003, 142, (1), 45-52.

728 52. Marc, J.; Mulner-Lorillon, O.; Boulben, S.; Hureau, D. e.; Durand, G. l.; Bella, R.,

729 Pesticide Roundup provokes cell division dysfunction at the level of CDK1/cyclin B activation.

730 Chemical Research in Toxicology 2002, 15, (3), 326-331.

733 TOC/ABSTRACT ART

Roundup &glyphosate Reproductive output

/t C! cc c\ / \ [ ? CCC? ? 1 V be c 'c c c I

4 Gonad transcript profiling & histology « Embryo survival & hatching