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The Ramazzini Institute 13-week study on glyphosate-based herbicides at human-equivalent dose in Sprague Dawley rats: study design and first in-life endpoints evaluation

Environmental Health volume 17, Article number: 52 (2018) Cite this article

Abstract

Background

Glyphosate-based herbicides (GBHs) are the most widely used pesticides worldwide, and glyphosate is the active ingredient of such herbicides, including the formulation known as Roundup. The massive and increasing use of GBHs results in not only the global burden of occupational exposures, but also increased exposure to the general population. The current pilot study represents the first phase of a long-term investigation of GBHs that we are conducting over the next 5 years. In this paper, we present the study design, the first evaluation of in vivo parameters and the determination of glyphosate and its major metabolite aminomethylphosphonic acid (AMPA) in urine.

Methods

We exposed Sprague-Dawley (SD) rats orally via drinking water to a dose of glyphosate equivalent to the United States Acceptable Daily Intake (US ADI) of 1.75 mg/kg bw/day, defined as the chronic Reference Dose (cRfD) determined by the US EPA, starting from prenatal life, i.e. gestational day (GD) 6 of their mothers. One cohort was continuously dosed until sexual maturity (6-week cohort) and another cohort was continuously dosed until adulthood (13-week cohort). Here we present data on general toxicity and urinary concentrations of glyphosate and its major metabolite AMPA.

Results

Survival, body weight, food and water consumption of the animals were not affected by the treatment with either glyphosate or Roundup. The concentration of both glyphosate and AMPA detected in the urine of SD rats treated with glyphosate were comparable to that observed in animals treated with Roundup, with an increase in relation to the duration of treatment. The majority of glyphosate was excreted unchanged. Urinary levels of the parent compound, glyphosate, were around 100-fold higher than the level of its metabolite, AMPA.

Conclusions

Glyphosate concentrations in urine showed that most part of the administered dose was excreted as unchanged parent compound upon glyphosate and Roundup exposure, with an increasing pattern of glyphosate excreted in urine in relation to the duration of treatment. The adjuvants and the other substances present in Roundup did not seem to exert a major effect on the absorption and excretion of glyphosate. Our results demonstrate that urinary glyphosate is a more relevant marker of exposure than AMPA in the rodent model.

Peer Review reports

Background

Glyphosate [IUPAC chemical name N-(phosphonomethyl)glycine] is the most widely applied pesticide worldwide and it is an active ingredient of all glyphosate-based herbicides (GBHs), including in the formulation “Roundup” [1, 2]. It is mainly marketed as a broad-spectrum systemic herbicide and crop desiccant [3]. The Asia-Pacific region represents the largest supplier of glyphosate active ingredient worldwide in terms of production.. In 2016, China contributed the largest share in the Asia Pacific, and is likely to remain a dominant market for years to come. The United State trails behind the Asia-Pacific market in the production of GBHs. Latin America, Middle East and Africa are expected to grow in terms of use at a significant rate during 2017–2025 [4]. Production and use of glyphosate have risen dramatically with the introduction in 1996 of genetically modified (GM) glyphosate tolerant crop varieties. In the United States (US) glyphosate is contained in over 750 products, particularly herbicides used for intensive GM crops that have built-in tolerance to glyphosate, but also in other products used in agriculture, forestry, urban, and home applications [5]. In 2015, 89% of corn, 94% of soybeans, and 89% of cotton cropped in the US were genetically modified to be glyphosate-tolerant [6]. Only a few data on the use of individual pesticides are available for certain countries in the European Union (EU), making it difficult to find out how much glyphosate is being used by farmers [7]. However, surveys in individual countries give some indication. Glyphosate is the top ranked herbicide in United Kingdom arable crop production [8]. In Denmark, glyphosate accounts for 35% of all pesticides used in agricultural production [9]. In Germany, it has been estimated that glyphosate is used on 4.3 million hectares (39%) of agricultural land each year, with nearly two thirds applied to just 3 crops - oilseed rape, winter wheat and winter barley [10]. The EU has a strict regulation regarding the planting of GM crops (Directive EU 2015/412) [11] and GBHs are mainly applied to cereals for post-harvest desiccation purposes (wheat, rye, triticale, barley and oats), oilseeds (rapeseed, mustard seed and linseed), orchards and vineyards [12].

The massive and increasing use of GBHs leads to a global burden of occupational exposures in manufacturing workers and GBH applicators (farmers), as well as increasing exposures in the general population, as demonstrated by environmental contamination from glyphosate residues found in air [13], groundwater [14, 15], drinking-water [16], crops [17, 18], food [19, 20] and animal feed [21]. Microbial biodegradation of glyphosate occurs in soil, aquatic sediment and water. The main pathway of biodegradation of glyphosate appears to be by splitting the C–N bond to produce aminomethylphosphonic acid (AMPA), the major microbial metabolite [22]. In humans, the main exposure routes to glyphosate are inhalation and dermal exposure in the occupational setting and consumption of water and food for the general population [22]. The results of oral studies with [14C] glyphosate in rats, rabbits and goats indicate that absorption from the gastrointestinal tract is incomplete and amounts to up to 30% of the dose [23,24,25]. The most relevant routes of excretion following oral administration of glyphosate [14C] are feces (70–80%) and urine (20–30%) [26]. In rats, after a single oral administration of [14C] glyphosate, almost all radioactivity was detected in urine and feces, and the radiolabeled detected chemical was present as the unchanged parent compound [27,28,29]. Elimination through exhaled air was very low. AMPA was the only metabolite detected, accounting for only 0.2–0.3% of the applied dose of [14C] glyphosate [30]. The limited data currently available on glyphosate pharmacokinetics in vertebrates are insufficient to predict transport and fate of glyphosate in different mammalian tissues, organs and fluids in the body, and to determine whether or where bioaccumulation occurs, although animal metabolism studies indicate kidney and liver as target tissues [1].

The possible effects of GBHs on human health is the topic of intense public debate, for both its potential carcinogenic and non-carcinogenic effects, including endocrine disruption, neurotoxicity, developmental and reproductive toxicity, which might occur even at doses much lower than the ones considered for risk assessment, in particular during sensitive periods of life (such as fetal development) [5, 12, 31, 32]. Glyphosate, as the pure active substance, and GBHs may not be quite the same from the toxicological standpoint. Glyphosate formulations contain a number of so-called ‘inert’ ingredients or adjuvants to facilitate the uptake by plants, most of which are patented and not publicly known (in many countries the law does not require a full disclosure of pesticide ingredients). GBHs that contain surfactants and adjuvants might act differently than glyphosate alone [33, 34]. In fact, adjuvants might potentiate the toxic effects of glyphosate [35,36,37,38].

The Ramazzini Institute 13-week pilot study: aims and experimental design

The present pilot study is the first phase of an integrated long-term project on GBHs that we are conducting during the next 5 years [39]. The initial focus of our pilot study is to assess techniques and methods for glyphosate detection in different matrices (results presented here), then to evaluate target organ toxicity, genotoxicity and endocrine disrupting activities, together with omics and microbiome alterations (not presented here). In our pilot study, we exposed Sprague-Dawley (SD) rats to either glyphosate or Roundup, one of the most popular branded GBHs, with a dosage considered to be “safe”, the United States Acceptable Daily Intake (US ADI) of 1.75 mg/kg bw/day, defined as the chronic Reference Dose (cRfD) determined by the US EPA [40]. The design of the pilot study derives from the 13-week cohort protocol of the National Toxicology Program (NTP) guideline Modified One-Generation study (MOG) [39, 41]. It incorporates exposure during the perinatal period (i.e., gestation and lactation) and later for 13 weeks after the pups are weaned, evaluating standard sub-chronic toxicity and functional endpoints (e.g., sperm analysis, vaginal cytology, indices of puberty and sexual differentiation) to investigate possible effects on the reproductive and endocrine systems. In order to provide more information about specific modes of action, we further integrated the 13-week cohort NTP MOG design with transcriptome analyses of potential target tissues and gut microbiome evaluation at different time-points and life stages in both dams and their offspring. The whole-transcriptome analysis can provide important mechanistic information and support the pathological evaluation of target organs and hormone analysis. The gut microbiome evaluation is a novel endpoint representing the potential role of altered balance in the gut microbiota that relate to several health disorders such as metabolic diseases, hepatic, coronary and gastrointestinal diseases (e.g., inflammatory bowel disease) [32]. The experimental plan and the endpoints investigated in the study are presented in Table 1 and Table 2.

Table 1 Experimental plan
Full size table
Table 2 Summary of the endpoints and relative monitoring time points evaluated in the study, in dams and offspring (6-week and 13-week cohorts)
Full size table

The protocol of the pilot study commences with exposure from gestation day (GD) 6 (implantation) continuously through pregnancy and lactation. To satisfy the need to consider multiple effects across multiple life stages, at weaning the offspring were assigned to two testing cohorts at random, so as to have minimal differences in body weight among groups (standard deviation < 10% of the average). The first cohort (6-week cohort) was continuously dosed until full sexual maturity (Post Natal Day-PND 73 ± 2), then sacrificed. The second cohort (13-week cohort) was continuously dosed until adulthood (PND 125 ± 2), then sacrificed. Both cohorts were analyzed for post-natal developmental landmarks, microbiome, target organs toxicity and clinical pathology.

The design of the pilot study has been developed by the Ramazzini Institute in collaboration with all Institutions taking part in the overall Glyphosate Study. All of the in vivo experimental phases of the study were performed at the Ramazzini Institute, while the other collaborating Institutions have independently assessed different outcomes and endpoints of interest. In this paper, we present the study design, the first evaluation of in vivo parameters and the determination of glyphosate and its major metabolite AMPA in urine.

Methods

Experimental model

The study was conducted following the rules established by the Italian law regulating the use and humane treatment of animals for scientific purposes [Decreto Legislativo (D.Lgs.) N. 26, 2014. Attuazione della direttiva n. 2010/63/UE in materia di protezione degli animali utilizzati a fini scientifici. - G.U. Serie Generale, n. 61 del 14 Marzo 2014]. Before starting, the protocol was examined by the Internal Ethical Committee for approval. The protocol of the experiment was also approved and formally authorized by the ad hoc commission of the Italian Ministry of Health (ministerial approval n. 710/2015-PR). The experiment was performed on both male and female SD rats, which belong to the colony used at the Cesare Maltoni Cancer Research Center laboratories of the Ramazzini Institute (CMCRC/RI) for over 40 years. An animal disease screening program enforced by the Italian Health Authority and Research Organization for Animal Health is in place and ongoing on sentinel animals belonging to the RI colony.

Female breeders SD rats were placed individually in Polycarbonate cage (42x26x18cm; Tecniplast Buguggiate, Varese, Italy) with a single unrelated male until evidence of copulation was observed. After mating, matched females were housed separately during gestation and delivery. Newborns were housed with their mothers until weaning. Weaned offspring were housed, by sex and treatment group, not more than 3 per each cage. Cages were identified by a card indicating: study protocol code, experimental and pedigree numbers, dosage group. A shallow layer of white fir wood shavings served as bedding (supplier: Giuseppe Bordignon, Treviso, Italy). Analysis of chemical characteristics (pH, ashes, dry weight, specific weight) and possible contamination (metals, aflatoxin, polychlorobiphenyls, organophosphorus and organochlorine pesticides) of the bedding was performed by CONSULAB Laboratories (Treviso, Italy). The cages were placed on racks, inside a single room prepared for the experiment at 22 °C ± 3 °C temperature and 50 ± 20% relative humidity. Daily checks on temperature and humidity were performed. The light was artificial and a light/dark cycle of 12 h was maintained.

During the experiment SD rats received ad libitum the standard “Corticella” pellet feed supplied by Laboratorio Dottori Piccioni Srl (Piccioni Laboratory, Milan, Italy). The constituents of the diet are: ground corn (23%), barley milled (15%), soybean meal extract (20.6%), wheat middling (24%), wheat bran (2%), spray dried whey (2.5%), di-calcium phosphate (2%), calcium carbonate (1.1%), chicken meal (6%), carob bean gum (3%), sodium chloride (0.5%), mixed vitamins (0.3%). Every day, the animals drank fresh municipal tap water from glass bottles ad libitum. Both feed and water were periodically analyzed to identify possible chemical or microbiological contaminants or impurities; the analyses are included in the documentation of the experiment. The pelleted feed was tested for possible glyphosate contamination in compliance with Commission Regulation (EU) No 293/2013 [maximum residue levels (MRLs) < 1 mg/kg]. Tap drinking water was tested for possible glyphosate contamination in compliance with Directive 2008/105/EC, D.Lgs. 152/2006, Directive2006/118/EC (active substances in pesticides, including their relevant metabolites, degradation and reaction products < 0.1 μg/l).

Active ingredient glyphosate (Pestanal™ analytical standard, CAS number 1071–83-6, purity > 99,5%) was supplied from Sigma-Aldrich (Milan, Italy). The commercial formulation Roundup Bioflow (containing 360 g/L of glyphosate acid in the form of 480 g/l isopropylamine salts of glyphosate (41.5%), water (42.5%) and surfactant (16%; chemical name, CAS number and/or exact percentage have been withheld as a trade secret) was supplied from a local agricultural consortium (Consorzio Agrario dell’Emilia, Bologna, Italy). The original containers/bottles of glyphosate and Roundup were stored in its original container and kept in a ventilated storage cabinet at room temperature (22 °C ± 3 °C) throughout the study. Purity data for each batch of glyphosate and Roundup were provided by the supplier. The opening and the use date of the different batches of test substances were recorded in the raw data. An aliquot of each lot of the test article is maintained in the ventilated storage cabinet, until 5 years from the end of the main experiment. The solutions of glyphosate and Roundup were prepared by the addition of appropriate volume of tap drinking water.

Experimental plan

Each of twenty-four virgin female SD rats (17 weeks old, 270-315 g) was cohabited outbred with one breeder male rat of the same age and strain. Every day, the females were examined for presence of sperm. Gestational day (GD) 0 was defined as the one in which the sperm was found in vaginal smears. The day on which parturition was completed was designated as lactating day (LD) 0 for the dam and PND 0 for the offspring. Each dam and delivered litter was co-housed in common nesting box during the postpartum period. Following the NTP MOG design, on PND 28, thus 28 days after the last litter was delivered, the offspring were weaned and identified by ear punch according to the Jackson Laboratory system. Sequentially, they were allocated in the same treatment group of their mother in order to have 18 males (8 for the 6-week cohort and 10 for the 13-week cohort) and 18 females (8 for the 6-week cohort and 10 for the 13-week cohort) for each dose group. No more than 2 males and 2 females from the same litter were included in the same cohort/treatment group. Altogether, 108 SD rats (54 males and 54 females) were enrolled in the post-weaning treatment phase. The experimental plan of the pilot study is outlined in Table 1. A summary of the endpoints and relative monitoring time points evaluated in the pilot study, both in dams and in the offspring (6-week and 13-week cohorts) is presented in Table 2.

Two groups of SD rats were treated with either glyphosate or Roundup diluted in tap water administered ad libitum and one group received only tap water as control. Roundup was diluted in tap water in order to obtain an equivalent dose of glyphosate of 1.75 mg/kg bw/day. During gestational and lactational periods, embryos and newborns (F1) received the test compounds mainly through their dams (F0). Glyphosate and Roundup water formulations during these periods were freshly prepared on a daily base depending on individual body weight and water consumption of dams as measured at each scheduled time point (see below). After weaning, until the end of the experiment (PND 73 ± 2 or 125 ± 2), the test substances were administered in tap water to F1 animals on the basis of the average body weight and average water consumption per sex and per experimental group, as measured at each scheduled time point (see below). Males and females were considered separately because of their difference in weight gain, body weight and water consumption.

At least every week, the exposure doses were recalculated and registered. The actual levels of test compounds that reached the fetus during gestation or that were ingested postnatally by the offspring during the period of lactation were not estimated in the present study.

Animals were monitored during the entire experimental period. The following procedures were performed:

Health status control: from the start of the experiment, animals were checked three times daily, except on Sundays and non-working days, when they were only checked twice. All observed variations from normal status were recorded.

Clinical control: status, behavior and clinical observation on the experimental animals were checked before the start of the treatment, and at least every two days until the end of the experiment. Any findings listed below were then recorded: alterations of skin, hair, eyes and mucosa; modification in production of secretions or excretions and in autonomic activity; respiratory symptoms; postural changes or changes in walk; presence of tonic or clonic contractions; unusual stereotypes and behavior.

Dams’ body weights were recorded on GD 0, 3, 6 and then daily during gestation until parturition. During lactation, dams’ body weights were recorded at LD 1, 4, 7, 10, 13, 16, 19, 21 and 25 (last measurement before weaning). Pups’ body weight by sex and litter was determined on PND 1, 4, 7, 10, 13, 16, 19, 21 and 25. After weaning, the body weight was measured twice a week, until PND 73 ± 2, then weekly until PND 125 ± 2 and before terminal sacrifices; the means of individual body weights were calculated for each group and sex.

Dams’ feed and water consumption were recorded twice weekly during gestation (GD 0, 3, 6, 9, 12, 15, 18, 21), whereas during lactation were measured at LD 1, 4, 7, 10, 13, 16, 19, 21, 25 and 28.

After weaning the daily water and feed consumption per cage were measured twice a week, until PND 73 ± 2, then weekly until PND 125 ± 2; the means of individual consumptions were calculated for each group and sex.

The day before the terminal sacrifices, all the animals were located individually in metabolic cages and starved for around 16 h. During this time, the animals had free access to water alone or to the programmed test compound solutions. The day after, in the morning, samples of at least 5 ml of spontaneous urine from each animal were collected and put in separate labelled tubes. Urine samples for analysis of glyphosate and AMPA excretion were obtained from 3 dams/group and from 10 (5 males + 5 females) rats/group belonging to the 6-week and 13-week cohorts.

Glyphosate and aminomethylphosphonic acid (AMPA) detection

Analyses of glyphosate and its metabolite AMPA in drinking water, feed and urine were performed by Neotron Laboratories (Modena, Italy), an officially accredited laboratory by Accredia (Lab. N. 0026) according to European regulation UNI CEI EN ISO/IEC 17025:2005. The specification and results are maintained in the experimental documentation. The analytical method is based on liquid chromatography tandem mass spectrometry (LC-MS/MS) [42,43,44,45]. The limit of quantification (LQ) for glyphosate and AMPA corresponded to 0.10 μg/l in water, 50 μg/kg in feed, and 1 μg/kg in urine.

Statistical analysis

Summary statistics, means ± standard deviations (sd), were calculated for continuous variables. For body weight, water and feed consumption over time further analyses were performed using multilevel mixed-effect linear regression models, to control for within subject correlation across time; moreover we have considered also the litter effect during the lactation period. Analysis of variance and Dunnett’s tests (when applicable) were also performed to compare body weight gain in different periods and consumption of food and water as mean consumption in several periods.

All tests were two tailed, with alpha set at 0.05. Statistical analyses were perfomed by using STATA version10 (Stata Corporation, College StationTexas, USA).

Results

In dams, during both gestation and lactation, body weight and weight gain were not statistically different among the different groups (Fig. 1 a-b). In both female and male offspring, post weaning body weights were homogenous and no statistically significant differences in body weight gain were observed among groups (Fig. 1 c-f). All 24 dams and 108 SD rats from the 6-week (48/48) and 13-week (60/60) cohorts survived until sacrifice.

Fig. 1
figure1

Average body weight: dams during gestation (a), treatment starting at gestation day 6 (↓); dams (b), male (c) and female (d) offspring during lactation; male (e) and female (f) offspring after weaning. At week 6 after weaning 8 male and 8 female pups per group were sacrificed

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Water and feed consumption during gestation and lactation were no different across the groups (Fig. 2 a-b and Fig. 3 a-b). Litter sizes were fully comparable among groups, with mean number of live pups: control group 13.6 (range 10–16); glyphosate group 13.3 (range 11–17); Roundup group 13.9 (range 11–16). Post weaning water and feed consumption were not affected by the treatment (Fig. 2 c-d and Fig. 3 c-d).

Fig. 2
figure2

Average water consumption: dams during gestation (a), treatment starting at gestation day 6 (↓); dams and litter (b) during lactation; male (c) and female (d) offspring after weaning. At week 6 after weaning 8 male and 8 female pups per group were sacrificed

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Fig. 3
figure3

Average feed consumption: dams during gestation (a), treatment starting at gestation day 6 (↓); dams and litter (b) during lactation; male (c) and female (d) offspring after weaning. At week 6 after weaning 8 male and 8 female pups per group were sacrificed

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No unexpected clinical signs or symptoms were observed in the experimental animals during the in vivo phase. In particular, there was no clinical evidence of alterations in activity or behavior, reflexes, the eye or skin, or the respiratory, gastrointestinal, genito-urinary and cardiovascular systems.

The results of glyphosate and AMPA urinary concentrations are reported in Table 3 and Fig. 4. The urinary concentration of both glyphosate and AMPA of SD rats treated with 1.75 mg/kg bw/day of glyphosate were comparable to the ones observed in SD rats treated with Roundup dose equivalent to 1.75 mg/kg bw/day, despite limited sample size and the large standard deviations. In the control group, as expected, the glyphosate and AMPA urinary levels were all below or close to the limit of quantitation (0.001 mg/kg). In the treated SD rats, the majority of glyphosate was excreted unchanged (as parent compound), with urinary levels about 100-fold higher than that of its metabolite AMPA. For example, glyphosate and Roundup treated females in the 13-week cohort presented mean urinary levels of glyphosate respectively of 1.354 mg/kg and 1.524 mg/kg, while the AMPA levels were respectively 0.013 mg/kg and 0.021 mg/kg. In glyphosate and Roundup treated SD rats, a time-dependent increase in the mean urinary concentration of glyphosate was observed. In glyphosate and Roundup treated males, an approximate 2-fold increase of mean urinary concentration of glyphosate in the 13-week cohort (animals exposed prenatally until 125 ± 2 days after birth) compared to the 6-week cohort (animals exposed prenatally until 73 ± 2 days after birth) was observed. In glyphosate treated females, the 6-week cohort (animals exposed prenatally until 73 ± 2 days after birth) showed a 2-fold higher value of mean urinary concentration of glyphosate than the dams after weaning (exposed for 49 ± 2 days), while the 13-week cohort (animals exposed prenatally and 125 ± 2 days after birth) showed a 1.5-fold increase compared to the 6-week cohort. In the Roundup treatment group, the increase was less steep, but the time-dependent pattern was still evident. In glyphosate and Roundup treated SD rats, the levels of AMPA were comparable at the different time points in both males and females. In these animals, large standard deviations of the values of AMPA concentrations in urine have been observed, in particular for values close to the limit of quantitation as in the control groups.

Table 3 Glyphosate and AMPA concentration in urine. Results are reported as mean ± standard deviations
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Fig. 4
figure4

Average urinary concentrations of glyphosate and AMPA, expressed in mg/kg, collected at terminal sacrifices. Dams glyphosate (a) and AMPA (b) excretion; 6-week cohort male and female offspring; glyphosate (c) and AMPA (d) excretion; 13-week cohort male and female pups Glyphosate (e) and AMPA (f) excretion

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Discussion

Survival, body weights, food and water consumption of SD rats were not affected by the treatment with glyphosate and Roundup. Clinical changes in the animals were not observed in the various groups. Overall, both glyphosate and Roundup treatments seemed to be well tolerated, which is consistent with previous experiments performed by the US NTP [26].

Glyphosate and Roundup exposure led to comparable concentrations of glyphosate and AMPA in urine, indicating that systemic exposure does occur at the selected exposure level of 1.75 mg//kg bw/day, corresponding to the US ADI. The bioavailability of glyphosate in our study is also supported by the evident increase of glyphosate concentration in urine in relation to the length of treatment. The adjuvants and the other substances present in Roundup did not seem to exert a major effect on the absorption and excretion of glyphosate, even though mean values of glyphosate seem to be somewhat higher in the Roundup treated group. The levels in urine were also comparable between the two sexes; however, a consistent inter-individual variability was observed. In rats, glyphosate in urine appears to be the most accurate biomarker of exposure to GBHs. In fact, our results confirm previous evidence that in rodents most of the administered dose of glyphosate (98%) is excreted as unchanged parent compound, whereas the metabolite AMPA in urine is at around 0.2–0.3% of the administered dose [46]. Furthermore, with the level of exposure to glyphosate used in this pilot study, AMPA urinary values of treated animals (0.011–0.027 mg/kg) were already close to the chromatographic LQ (0.001 mg/kg) and this might limit the reliability of the measures. On the other hand, glyphosate concentration in urine of treated animals (0.480–2.280 mg/kg) resulted up to 100-fold higher than the AMPA concentration and at least 500-fold higher than the chromatographic LQ (0.001 mg/kg). Therefore, in order to assess exposure to glyphosate in rats, in particular at doses that are equal or lower than the one used in this pilot study (1.75 mg/kg bw/day), glyphosate appears to be the biomarker of choice.

The presence of negligible levels of glyphosate (0.003–0.013 mg/kg), close to the chromatographic LQ (0.001 mg/kg), in some of the urine of the control groups might reflect an ubiquitous environmental contamination at ultra-low doses of glyphosate, which is consistent with previous reports from other authors [21]. As the current limit of quantitation of glyphosate in HPLC for pelleted animal feed is 0.050 mg/kg, this represents a technical limiting factor for testing ultra-low doses of glyphosate. As reported by a recent inter laboratory comparative study on the quantitative determination of glyphosate at low levels, caution should be taken when interpreting results if the tested doses of glyphosate are close to the LQ of HPLC [47].

It is noteworthy that the commercial formulation used in this study, Roundup Bioflow, was the representative formulated product recently evaluated for the renewal of the approval of glyphosate in EU and considered in the European Food Safety Authority peer review (MON 52276) [48].

Our results seem particularly relevant in light of the massive global burden of exposure to glyphosate, as shown by the exponential increase in the last 20 years of the levels of glyphosate and AMPA measured in the urine of the general population in Germany [49] and in the US [50].

Conclusion

We performed a pilot study on the health effects of glyphosate and its formulation Roundup administered at currently admitted doses (US ADI = 1.75 mg/kg bw/day) to SD rats. In this paper, we described the study design, the first evaluation of in vivo parameters and the determination of glyphosate and its major metabolite AMPA in urine. The treatment with either glyphosate or Roundup seemed to be overall well tolerated, consistently with previous experiments performed by the US NTP [26]. Both glyphosate and Roundup exposure led to comparable urinary concentrations of glyphosate and AMPA with an increasing pattern of glyphosate excreted in urine in relation to the duration of treatment, indicating the systemic bioavailability of the active substance and a possible mechanism of bioaccumulaton. The adjuvants and the other substances present in Roundup did not seem to exert a major effect on the absorption and excretion of glyphosate. Our results confirm that, in rodents, glyphosate in urine is the much more relevant marker of exposure than AMPA in particular at doses that are equal or lower than the one used in this pilot study (1.75 mg/kg bw/day). The evaluation of different outcomes and endpoints of interest (i.e., pathology of target organs, molecular toxicity, genotoxicity, endocrine disrupting activities, microbiome, developmental toxicity, etc.) is currently ongoing in the different partner laboratories of the project.

Abbreviations

AMPA:

Aminomethylphosphonic acid

CMCRC:

Cesare Maltoni Cancer Research Center

EU:

European Union

GBH:

Glyphosate-based herbicides

GD:

Gestational day

GM:

Genetically modified

LC-MS/MS:

Liquid chromatography tandem mass spectrometry

LD:

Lactating day

LQ:

Limit of Quantification

MOG:

Modified One-Generation study

NTP:

National Toxicology Program

PND:

Post Natal Day

RI:

Ramazzini Institute

SD:

Sprague-Dawley

US ADI:

United States Acceptable Daily Intake

References

  1. 1.

    Myers JP, Antoniou MN, Blumberg B, Carroll L, Colborn T, Everett LG, et al. Concerns over use of glyphosate-based herbicides and risks associated with exposures: a consensus statement. Environmental health : a global access science source. 2016;15:19. https://doi.org/10.1186/s12940-016-0117-0.

  2. 2.

    Benbrook CM. Trends in glyphosate herbicide use in the United States and globally. Environ Sci Eur. 2016;28(1):3. https://doi.org/10.1186/s12302-016-0070-0.

  3. 3.

    Smith EA, Oehme FW. The biological activity of glyphosate to plants and animals: a literature review. Vet Hum Toxicol. 1992;34(6):531–43.

  4. 4.

    Research TM. “Herbicides Market by product (Acetohlor, 2,4-D, Glyphosate, Atrazine), by application (Oilseeds & Pulses, Cereals & grains, Fruits & vegetables) - Global Industry Analysis, Size, Share, Growth, Trends, and Forecast, 2017–2025”. Available at: https://www.transparencymarketresearch.com/herbicides-market.html. 2017.

  5. 5.

    IARC. Glyphosate. In: Some organophosphate insecticides and herbicides: diazinon, glyphosate, malathion, parathion, and tetrachlorvinphos. Vol 112. IARC Monogr Prog, 1–92. 2015.

  6. 6.

    USDA. Adoption of Genetically Engineered Crops in the U.S.. Economic Research Service 2015;Retrieved 20 December 2017..

  7. 7.

    Garthwaite D, Sinclair C, Glass R, Pote A, Trevisan M, Sacchettini G, et al. Collection of pesticide application data in view of performing environmental risk assessments for pesticides. EFSA Supporting Publications. 2015;12(7)

  8. 8.

    Garthwaite D, Barker I, Parrish G, Smith L, Chippindale C, Pietravalle S. Pesticide usage survey report 235. Arable Crops in UK 2010 (Including Aerial Applications 2010). 2010.

  9. 9.

    DEPA. Annual Pesticides Statistics 2009. 2009.

  10. 10.

    Steinmann HH, Dickeduisberg M, Theuvsen L. Uses and benefits of glyphosate in German arable farming. Crop Prot. 2012;42:164–9.

  11. 11.

    EU. Directive (EU) 2015/412 of the European Parliament and of the Council of 11 March 2015 amending Directive 2001/18/EC as regards the possibility for the Member States to restrict or prohibit the cultivation of genetically modified organisms (GMOs) in their territory. 2015.

  12. 12.

    EFSA. European Food Safety Authority. Conclusion on the peer review of the pesticide risk assessment of the active substance glyphosate. EFSA J. 2015;13:4302.

  13. 13.

    Majewski MS, Coupe RH, Foreman WT, Capel PD. Pesticides in Mississippi air and rain: a comparison between 1995 and 2007. Environ Toxicol Chem. 2014;33(6):1283–93. https://doi.org/10.1002/etc.2550.

  14. 14.

    ISPRA. National Report of Pesticides in Water (2013–2014) [in italian, "Rapporto Nazionale pesticidi nelle acque dati 2013–2014"] Rapporti. 2016;244/2016.

  15. 15.

    Battaglin WA, Meyer MT, Kuivila KM, Dietze JE. Glyphosate and its degradation product AMPA occur frequently and widely in U.S. soils, surface water, groundwater, and precipitation. J Am Water Resour Assoc. 2014;50 https://doi.org/10.1111/jawr.12159.

  16. 16.

    Rendón-von Osten J, Dzul-Caamal R. Glyphosate residues in groundwater, drinking water and urine of subsistence farmers from intensive agriculture localities: a survey in Hopelchén, Campeche, Mexico. Int J Environ Res Public Health. 2017;14(6):595. https://doi.org/10.3390/ijerph14060595.

  17. 17.

    Cuhra M. Review of GMO safety assessment studies: glyphosate residues in roundup ready crops is an ignored issue. Environ Sci Eur. 2015;27 https://doi.org/10.1186/s12302-015-0052-7.

  18. 18.

    USDA. Agricultural Marketing Service. Pesticide data program annual summary, program year 2011. In: Appendix C distribution of residues in soybean by pesticide. Washington, D.C: U.S. Department of Agriculture; 2013.

  19. 19.

    EFSA. The 2014 European Union report on pesticide residues in food. EFSA journal. 2016;14(10):e04611-n/a) https://doi.org/10.2903/j.efsa.2016.4611.

  20. 20.

    PRIF. Expert Committee On pesticide residues in food (PRiF): annual report for 2016. Available at: https://www.gov.uk/government/publications/expert-committee-on-pesticide-residues-in-food-prif-annual-report.

  21. 21.

    Mesnage R, Defarge N, Rocque LM, Spiroux de Vendomois J, Seralini GE. Laboratory rodent diets contain toxic levels of environmental contaminants: implications for regulatory tests. PLoS One. 2015;10(7):e0128429. https://doi.org/10.1371/journal.pone.0128429.

  22. 22.

    WHO. Glyphosate and AMPA in drinking-water. Background document for development of WHO Guidelines for Drinking-water Quality copyright World Health Organization. 2005:9.

  23. 23.

    Powles P. 14C-glyphosate: absorption, distribution, metabolism and excretion following repeated oraladministration to the dairy goat. Unpublished report no. 676/9–1011, dated 7 November 1994, from Hazle-ton Europe, Harrogate, England. Submitted to WHO by Cheminova a/S, Lemvig, Denmark. 1994.

  24. 24.

    Colvin L, Miller J. CP 67573 Residue and metabolism. Part 9: the metabolism of N-phosphonmethylglycine-14C (CP 67573-14C) in the rabbit. Unpublished report. 1973(298).

  25. 25.

    Brewster DW, Warren J, Hopkins WE. Metabolism of glyphosate in Sprague-Dawley rats: tissue distribution, identification, and quantitation of glyphosate-derived materials following a single oral dose. Fundam Appl Toxicol. 1991;17(1):43–51.

  26. 26.

    NTP. NTP technical report on the toxicity studies of Glyphosate (CAS No. 1071-83-6) Administered In Dosed Feed To F344/N Rats And B6C3F1 Mice. Toxicity report series. 1992;16:1–D3.

  27. 27.

    Davies D. Glyphosate acid: excretion and tissue retention of a single oral dose (1000mg/kg) in the rat. In: Unpublished report no CTL/P/4942; 1996.

  28. 28.

    Davies D. Glyphosate acid: excretion and tissue retention of a single oral dose (10 mg/kg) in the rat. Unpublished report no CTL/P/4940, Dated. 1996.

  29. 29.

    Davies D. Glyphosate acid: excretion and tissue retention of a single oral dose (10 mg/kg) in the rat following repeat dosing. Unpublished report no CTL/P/4944, Dated. 1996.

  30. 30.

    Howe R, Chott R, McClanahan R. Metabolism of glyphosate in Spague–Dawley rats. II. Identification, characterization, and quantitation of glyphosate and its metabolites following intravenous and oral administration. Unpublished report. St Louis, MO: Monsanto Environmental Health Laboratory; 1988.

  31. 31.

    ECHA. ECHA’s Committee for Risk Assessment (RAC). https://echa.europa.eu/-/echa-s-opinion-on-classification-of-glyphosate-published.. 2017.

  32. 32.

    Shehata AA, Schrodl W, Aldin AA, Hafez HM, Kruger M. The effect of glyphosate on potential pathogens and beneficial members of poultry microbiota in vitro. Curr Microbiol. 2013;66(4):350–8. https://doi.org/10.1007/s00284-012-0277-2.

  33. 33.

    Mullin CA, Fine JD, Reynolds RD, Frazier MT. Toxicological risks of agrochemical spray adjuvants: Organosilicone surfactants may not be safe. Front Public Health. 2016;4:92. https://doi.org/10.3389/fpubh.2016.00092.

  34. 34.

    Landrigan PJ, Benbrook C. GMOs, herbicides, and public health. N Engl J Med. 2015;373(8):693–5. https://doi.org/10.1056/NEJMp1505660.

  35. 35.

    Coalova I, Rios de Molina Mdel C, Chaufan G. Influence of the spray adjuvant on the toxicity effects of a glyphosate formulation. Toxicology in vitro : an international journal published in association with BIBRA. 2014;28(7):1306–11. https://doi.org/10.1016/j.tiv.2014.06.014.

  36. 36.

    Mesnage R, Bernay B, Seralini GE. Ethoxylated adjuvants of glyphosate-based herbicides are active principles of human cell toxicity. Toxicology. 2013;313(2–3):122–8. https://doi.org/10.1016/j.tox.2012.09.006.

  37. 37.

    Defarge N, Takacs E, Lozano VL, Mesnage R, Spiroux de Vendomois J, Seralini GE, et al. Co-Formulants in glyphosate-based herbicides disrupt aromatase activity in human cells below toxic levels. Int J Environ Res Public Health. 2016;13(3) https://doi.org/10.3390/ijerph13030264.

  38. 38.

    Williams GM, Kroes R, Munro IC. Safety evaluation and risk assessment of the herbicide roundup and its active ingredient, glyphosate, for humans. Regulatory toxicology and pharmacology : RTP. 2000;31(2 Pt 1):117–65. https://doi.org/10.1006/rtph.1999.1371.

  39. 39.

    Manservisi F, Babot Marquillas C, Buscaroli A, Huff J, Lauriola M, Mandrioli D, et al. An integrated experimental Design for the Assessment of multiple toxicological end points in rat bioassays. Environ Health Perspect. 2016; https://doi.org/10.1289/ehp419.

  40. 40.

    EPA. Re-registration Eligibility Decision (RED) Glyphosate: EPA-738-R-93-014. Washington, DC: US Environmental Protection Agency, Office of Pesticide Programs and Toxic Substances; 1993.

  41. 41.

    NTP. NTP’s Modified One-Generation Reproduction Study 2011.

  42. 42.

    Granby K, Johannesen S, Vahl M. Analysis of glyphosate residues in cereals using liquid chromatography-mass spectrometry (LC-MS/MS). Food Addit Contam. 2003;20(8):692–8. https://doi.org/10.1080/0265203031000109477.

  43. 43.

    FDA. Pesticide analytical manual vol. II -method I: "method of analysis for residues of 2-chloroethylphosphonic acid (ethephon) in pinneapples. Pesticide Reg. Sec 180:300. 2002.

  44. 44.

    FDA. Pesticide Analytical Manual Vol. II -Method I. "gas chromatographic determination of residues of Fosetyl-Al and phosphorous acid in pineapples". Pesticide Reg. Sec. 2002;180:415.

  45. 45.

    Kubilius DT, Bushway RJ. Determination of maleic hydrazide in pesticide formulations by capillary electrophoresis. Journal of AOAC International (USA). 1998;

  46. 46.

    IPCS. Glyphosate. Geneva, world health organization, International Programme on Chemical Safety (Environmental Health Criteria 159). 1994.

  47. 47.

    Simonetti E, Cartaud G, Quinn RM, Marotti I, Dinelli G. An Interlaboratory comparative study on the quantitative determination of glyphosate at low levels in wheat flour. J AOAC Int. 2015;98(6):1760–8. https://doi.org/10.5740/jaoacint.15-024.

  48. 48.

    European Food Safety A. Peer review of the pesticide risk assessment of the potential endocrine disrupting properties of glyphosate. EFSA Journal 2017;15(9):e04979-n/a doi:102903/jefsa20174979.

  49. 49.

    Conrad A, Schroter-Kermani C, Hoppe HW, Ruther M, Pieper S, Kolossa-Gehring M. Glyphosate in German adults - time trend (2001 to 2015) of human exposure to a widely used herbicide. Int J Hyg Environ Health. 2017;220(1):8–16. https://doi.org/10.1016/j.ijheh.2016.09.016.

  50. 50.

    Mills PJ, Kania-Korwel I, Fagan J, McEvoy LK, Laughlin GA, Barrett-Connor E. Excretion of the herbicide glyphosate in older adults between 1993 and 2016. JAMA. 2017;318(16):1610–1. https://doi.org/10.1001/jama.2017.11726.

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Acknowledgements

We thank the over 30,000 associates and volunteers of the Ramazzini Institute that made this pilot study possible through their commitment and generosity. We thank the Municipality of Bologna, the Emilia-Romagna Region, and the International Society of Doctors for Environment for organizing several events to promote this pilot study; “Coop Reno” and “Coopfond Fondo Mutualistico Legacoop” for supporting our research activity.

Funding

This work was funded by Institution fund of the Ramazzini Institute, Bologna, Italy.

Availability of data and materials

All raw data recorded and used during the current study are available from the corresponding author on reasonable request.

Author information

Author notes

  1. Simona Panzacchi and Daniele Mandrioli contributed equally to this work.

Affiliations

  1. Cesare Maltoni Cancer Research Center (CMCRC), Ramazzini Institute (RI), Via Saliceto, 3, 40010 Bentivoglio, Bologna, Italy
    • Simona Panzacchi
    • , Daniele Mandrioli
    • , Fabiana Manservisi
    • , Luciano Bua
    • , Laura Falcioni
    •  & Fiorella Belpoggi
  2. Department of Agricultural Sciences, University of Bologna, Viale Fanin 44, 40127, Bologna, Italy
    • Daniele Mandrioli
    •  & Giovanni Dinelli
  3. Department of Veterinary Medical Sciences, University of Bologna, Via Tolara di Sopra 50, 40064 Ozzano dell’Emilia, Bologna, Italy
    • Fabiana Manservisi
    • , Marcella Spinaci
    •  & Giovanna Galeati
  4. Department of Statistical Sciences, University of Bologna, Via Belle Arti 41, 40126, Bologna, Italy
    • Rossella Miglio
  5. Department of Food safety, Nutrition and Veterinary Public Health, Istituto Superiore di Sanità, Viale Regina Elena 299, 00161, Rome, Italy
    • Alberto Mantovani
    •  & Stefano Lorenzetti
  6. Department of Genetics and Genomic Sciences, Icahn School of Medicine at Mount Sinai, 1425 Madison Ave, New York, NY, 10029, USA
    • Jianzhong Hu
  7. Department of Environmental Medicine and Public Health, Icahn School of Medicine at Mount Sinai, New York, USA
    • Jia Chen
  8. Department of Environmental and Occupational Health, Milken Institute School of Public Health, The George Washington University, 950 New Hampshire Ave, Washington, DC, 20052, USA
    • Melissa J. Perry
  9. Arnhold Institute for Global Health, Icahn School of Medicine at Mount Sinai, 1216 Fifth Avenue, New York, NY, 10029, USA
    • Philip J. Landrigan
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  1. Simona Panzacchi
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Contributions

All authors provided substantial contributions to the conception/design of the work, acquisition, analysis or interpretation of the data, revised the manuscript critically, and approved the final version for submission. FM, SP, DM participated in the design of the study, performed the animal experiments and sample collection, and drafted the manuscript. LB and LF performed the animal experiments and sample collection. FB supervised the study, participated in the design of the study and helped to draft the manuscript. MS, GG, GD, RM, AM, SL, JH, JC, MJP, PJL, helped to draft the manuscript. All authors read and approved the final manuscript.

Corresponding author

Correspondence to Fiorella Belpoggi.

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Panzacchi, S., Mandrioli, D., Manservisi, F. et al. The Ramazzini Institute 13-week study on glyphosate-based herbicides at human-equivalent dose in Sprague Dawley rats: study design and first in-life endpoints evaluation. Environ Health 17, 52 (2018). https://doi.org/10.1186/s12940-018-0393-y

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Keywords

  • Glyphosate
  • Roundup
  • 13-week
  • Sprague-Dawley rat
  • Glyphosate based herbicides
  • GBH

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