Over the past decade, abnormalities have been documented in white-tailed deer (Odocoileus virginianus) in west-central Montana. Hypotheses proposed to explain these anomalies included contact with endocrine disrupting pesticides, such as imidacloprid. We evaluated the effects of imidacloprid experimentally at the South Dakota State University Wildlife and Fisheries Captive Facility where adult white-tailed deer females and their fawns were administered aqueous imidacloprid (an untreated control, 1,500 ng/L, 3,000 ng/L, and 15,000 ng/L). Water consumption, thyroid hormone function, behavioral responses, and skull and jawbone measurements were compared among treatments. Additionally, liver, spleen, genital, and brain imidacloprid concentrations were determined by an enzyme-linked immunosorbent assay (ELISA). Results indicated that 1) control deer consumed more water than treatment groups, 2) imidacloprid was present in the organs of our control group, indicating environmental contamination, 3) as imidacloprid increased in the spleen, fawn survival, thyroxine levels, jawbone lengths, body weight, and organ weights decreased, 4) adult female imidacloprid levels in the genitals were negatively correlated with genital organ weight and, 5) behavioral observations indicated that imidacloprid levels in spleens were negatively correlated with activity levels in adult females and fawns. Results demonstrate that imidacloprid has direct effects on white-tailed deer when administered at field–relevant doses.
Neonicotinoids are a broad-spectrum insecticide predominantly used as seed dressings on major field crops and are additionally used as sprays in crop production, in managing household pests, and in deterring pests on domesticated animals1. Neonicotinoids derive their toxicity from agonistically binding to nicotinic acetylcholine receptors (nAChRs) on the post-synaptic nerve membrane and firing nerve impulses in a manner that is uncontrollable and uninterrupted1,2,3,4,5,6,7. Neonicotinoids were first developed in the 1990s8, gained popularity from 2003-20119, and are now the most widely used pesticides in the world10.
Popularity of neonicotinoids is due to their advertised high toxicity to insects and low toxicity to vertebrates1. Additionally, neonicotinoids have gained popularity by their ability to systemically protect plants while reducing application inputs for farmers10. In 2014, over 3.3 million kg of neonicotinoids (including acetamiprid, clothianidin, dinotefuran, imidacloprid, thiacloprid, and thiamethoxam) were used in the United States (excluding Hawaii and Alaska) on pasture hay, alfalfa, orchards, grapes, rice, vegetables, fruit, cotton, wheat, soybeans, corn, and other crops11. In South Dakota, more than 94% of U.S. corn and at least 50% of U.S. soybeans12 are treated with one of the three neonicotinoids: clothianidin, imidacloprid, or thiamethoxam13,14,15.
Neonicotinoids are widely found in the environment for numerous reasons. First, only a small quantity (2–20%) of the seed-coated insecticide is absorbed by the developing plant; the remainder is released into the environment through leaching, drainage, run-off, or snowmelt16,17. Neonicotinoids are highly water soluble18; they are prevalent in diverse water bodies in the United States, Canada, Australia, Europe, and Asia17. Moreover, under the right conditions, neonicotinoids can persist in the soil, sometimes for many years1. Finally, untreated plants associated with cropland are often contaminated by neonicotinoids due to the systemic nature of these chemicals19. The widespread use of neonicotinoids provides numerous opportunities for exposure to non-target, beneficial species via the water, soil, and contaminated plant tissues.
In addition to their documented effects on beneficial insects, neonicotinoids adversely affect non-target vertebrates as well, including rats (Rattus norvegicus: reduced sperm production, reduced offspring weight, increased abortions, skeletal abnormalities, thyroid lesions, atrophy of retina, reduced weight gain of offspring, oxidative stress, and neurobehavioral deficits), mice (Mus musculus: suppressed cell-mediated immune response and prominent histopathological alterations in spleen and liver), rabbits (Sylvilagus sp: increased frequency of miscarriage and premature births), red-legged partridges (Alectoris rufa: reduced adult and chick survival, fertilization rate, and immune response), Nile tilapia (Oreochromis niloticus: extensive disintegration of testicular tissue and changes to gonads), Medaka (Oryzias latipes: juvenile stress led to ectoparasite infestation), and black-spotted pond frogs (Rana nigromaculata: DNA damage at very low concentrations)20. To our knowledge, no information is available on potential effects on large mammals, such as white-tailed deer (Odocoileus virginianus).
Over the past decade, morphological and developmental abnormalities have been documented in white-tailed deer in west-central Montana. Of 254 male deer of various ages, 67% showed genital developmental abnormalities such as mispositioned and undersized scrota and ectopic testes21; these abnormalities were documented for accident-killed and injured cervids21. Hoy et al.21 suggested that genital anomalies could be caused by endocrine disrupting pesticides but stated that, based on the information available, no cause and effect could be justified. In addition, from 2000 to 2009, brachygnathia superior (i.e., mandibular prognathia or underbite) increased from 0% to 70% for white-tailed deer that were collected from west-central (accident killed) and throughout (hunter harvested) Montana22. Underbite is a characteristic of congenital hypothyroidism, which has been documented in South Dakota23, and is nearly always associated with fetal thyroid hormone function22, but the cause has not been empirically determined for this observation.
We hypothesized that imidacloprid would have sub-lethal and potentially lethal effects on adult female and fawn white-tailed deer. We predicted that adult females, especially in the high treatment group, would have reduced Free Triiodothyronine (FT3) and Free Thyroxine (FT4) levels, presence of imidacloprid in milk, and reduced activity associated with exposure to imidacloprid. We also predicted that fawns exposed to imidacloprid at relatively high treatment levels would have abnormal genital organs, lowered FT3 and FT4 levels, reduced activity, and a high prevalence of under bite.
Our research study was conducted at the South Dakota State University Wildlife and Fisheries Captive Research Facility in Brookings County, South Dakota (44°20′N, 96°47′W). This facility housed white-tailed deer (beginning in about 1998) on 4 ha; the facility is double fenced with 3-m high woven wire. The facility is situated adjacent to agricultural fields normally planted to corn or soybeans, and is surrounded by a shelterbelt of trees. Mean annual temperatures were 7.4 °C (ranged from −28.8 °C and 34.4 °C) and 7.8 °C (−35 °C to 32.8 °C) in 2015 and 2016, respectively. Additionally, daily annual precipitation was 0.18 cm (0.03 cm to 5.2 cm) and 0.2 cm (from 0.3 cm to 7 cm) in 2015 and 2016, respectively. Finally, daily annual snowfall was 0.3 cm (0.3–17.8 cm) and 0.3 cm (0.3–11.4 cm) in 2015 and 2016, respectively24.
Twenty adult white-tailed deer were randomly selected for the experiment and bred; parturition occurred in May and June of each experimental year. Adult females were separated into four treatments (care was taken to separate adult females so that age and weight were uniformly distributed): control (n = 4), low (n = 4), moderate (n = 5), and high (n = 7) (the moderate and high treatment groups had a larger sample size to reduce the standard error for our response variable). Deer were housed in pens of similar size (control = 130 m2/deer, low = 175 m2/deer, moderate = 123 m2/deer, high = 112 m2/deer in 2015 and 165 m2/deer in 2016). All deer were fed rations that included soy hulls, shelled corn, and alfalfa hay ad libitum.
Adult females were administered aqueous imidacloprid (Product # 37984, Sigma Aldrich St. Louis, MO) from May until October to mimic free water availability within the Dakotas. We added 0 ng/L, 1,500 ng/L, 3,000 ng/L, and 15,000 ng/L of imidacloprid to the control, low, moderate, and high treatments, respectively. The low and moderate concentrations were similar to wetland levels found in groundwater in Wisconsin (detected in 24% of the groundwater sample and ranged from 260–3,340 ng/L); however, they were greater than levels found in rural streams in Iowa (detected in 23% of streams sampled and ranged from <2–42.7 ng/L) or in Canadian (Saskatchewan) wetlands (detected in 12% of wetlands and ranged from 7.1–256 ng/L)25. Our high treatment was intended to invoke an effect and therefore, was much greater than documented in free water. Deer were provided with a 60.6 L tub that contained 37.8 L of water treated with the appropriate amount of imidacloprid depending on the group (control, low, moderate, high). Deer consumed the water treated with imidacloprid ad libitum. Water levels were checked daily and refilled with the appropriate imidacloprid treated water when empty or less than 3 cm from the bottom (every 1–2 d) of containers. When refilling occurred, each tub was rinsed thoroughly and excess water was poured into 189 L tubs provided by the SDSU Environmental Health and Safety office.
Fawns born to adult females in the study were included in our experiment. On the day of parturition, each fawn was handled minimally with gloves to determine body mass and sex; fawns also were fitted with ear tags. To mimic natural water availability, fawns were not prevented from consuming the imidacloprid in water. Facilities and techniques for research were approved by the South Dakota State University Institutional Animal Care and Use Committee (IACUC number 15–055 A) and followed guidelines by the American Society of Mammologists26.
During experiments, water tubs housing aqueous imidacloprid were weighed daily to determine the volume of water consumed per group. Analysis of variance (ANOVA) was performed to compare water consumption among treatment and control groups with date used as a covariate. To detect imidacloprid concentrations as the imidacloprid water was consumed, a 3-d experiment was conducted. On day 1, the appropriate treatment or control group concentrations were created in five, 63 L galvanized tubs. On day 2, 50% of the water was removed from all tubs. On the third day, nearly all water was removed from the tubs, leaving only enough water to coat the bottom of tubs. Samples (15 mL) were collected daily from each tub. This procedure mimicked water level reductions due to deer consumption. Imidacloprid samples were analyzed using ELISA (enzyme-linked immunosorbent assay; Abraxis, Warminister, PA; See Section 4.7 for procedures).
Collection of blood samples
Blood samples were collected from adult females and fawns in treatments using BD Vacutainer Serum tubes (Becton, Dickinson, and Company, Franklin, NJ). We collected up to 12 mL of blood from the saphenous vein approximately monthly during treatments while deer were held in a chute (Priefert Wildlife Equipment Deer Chute; Priefert®, Mount Pleasant, TX). We collected blood samples (1–10cc from the saphenous or jugular) from fawns twice; 1 wk after parturition and at approximately 5 mo of age. Blood samples were refrigerated until processed to extract serum (1 h to 2 d). Upon reaching the lab, blood samples were centrifuged (Ultra-8V; LW Scientific, Lawrenceville, GA) for 15 min at 280 × g to separate serum for testing FT3 (free triiodothyronine) and FT4 (free thyroxine) hormones.
FT3 and FT4 thyroid hormones reflect the ability of the deer to utilize body fat reserves, regulate basal metabolic rate, and control thermal regulation27. Serum from blood samples was transferred to labeled 1.5 mL microcentrifuge tubes (BrandTech® Scientific Inc., Essex, CT), sealed, and frozen at −20 °C. These samples were then overnighted to the Diagnostic Center for Population and Animal Health at Michigan State University (Lansing, MI) for FT3 and FT4 testing. These assays were performed with commercially available solid-phase radioimmunoassay kits (FREE T3 Solid Phase Component System and Free T4 Solid Phase Component System, MP Biomedicals Diagnostics Division Orangeburg NY 10962). The volumes of sample, assay standards, and radioligand were used according to the manufacturer’s protocol. Incubation times for free T3 and free T4 assays were 2.5 h and 1.5 h, respectively, at 37 °C.
Focal sampling of behavioral observations were collected on treatment and control groups prior to death. Behaviors included eat, lay, lay/groom, lay/ruminate, stand/ruminate, run, stand, stand/groom, stand/nurse, and walk; for fawns, the behaviors lay/curl and lay/sleep also were recorded. Observations were conducted in 1 h blocks using an ethogram28. During time blocks, occurrences of behaviors were tallied and the duration of each behavior (in s) was recorded. Observations occurred between 6:00 and 16:00. In each session, an adult female or fawn was randomly chosen (without replacement) from each treatment and control group (n = 28 h for 2016 fawns and n = 21 h for adult females).
All deer in the experiment (adult females and fawns) were euthanized and subsequently necropsied using IACUC approved protocols. Fawns were euthanized at the end of each field season (October 2015 and 2016) and adult females were euthanized at the completion of the study (October 2016). Adult females and fawns were first tranquilized using xylazine (Bayer, Englewood, Colorado) and telezol (Zoetis, Parsippany-Troy Hills, New Jersey) when held in a Priefert deer chute and, once immobilized, were euthanized using euthanasia solution (MWI Veterinary Supply, Boise, ID) according to manufacturer’s suggested dosage. Once does and fawns were euthanized, they were frozen at −20 °C. All fawns and does in the experiment were necropsied at the South Dakota Animal Disease Research and Diagnostic Laboratory, South Dakota State University, Brookings, South Dakota.
Necropsies were performed by Dr. David Knudsen (assisted by E. Hughes Berheim). Liver, brain, spleen, and genital organs were extracted, weighed, and 2.54 cm3 samples were collected. Additionally, we collected fawn jawbones to determine length. Organ samples were then frozen at −20 °C until they could be analyzed using ELISA.
Imidacloprid levels were determined for each organ collected. Brain, liver, spleen, and genital samples were removed from the freezer, and a portion of each organ (0.5–0.75 g) was minced using a sterilized scalpel and placed into a polypropylene micro centrifuge tube. Water was added to the tube at a ratio of 1 mL:1 g tissue sample. Each mixture was shaken using a vortex (Thermo Scientific), heated in an 80 °C water bath for 10 min, and frozen at −20 °C. Frozen mixtures were thawed and centrifuged (Centrifuge 5424, Eppendorf) at 21,130 g for 1 min. The liquid was extracted and placed into separate micro centrifuge tubes; remaining solids in the organ samples and remaining liquid were refrozen. Liquid samples were vortexed and a 25 μL portion was extracted and placed into a separate microcentrifuge tube. The excess liquid also was stored frozen. The remaining liquid was mixed with 25 μL of water, vortexed for 5 s, and centrifuged for 2 s in preparation for the ELISA assay.
All samples were read at 450 nm using a microplate reader (uQuant, Biotek Instruments, Winooski, VT). Each plate had at least two standard curves of purified imidacloprid (Product number: 37894 SIGMA-ALDRICH, St. Louis, MO, USA). In preparation for the standard curve on each plate, samples from negative adult females were mixed together to account for the matrix effect of the organs and a stock solution of imidacloprid was created at 0.0, 0.03, 0.06, 0.13, 0.25, 0.5, 1.0, and 2.0 ppb. The standard curve on the ELISA plate contained 25 µL control organ in solution with 25 µL of the stock solution of imidacloprid, creating eight wells with concentrations that comprised one standard curve. We were unable to use the control organs in our standard curve because our experiment was unintentionally contaminated with imidacloprid; therefore, we used the deer sample with the lowest absorbance value as our baseline for quantifying imidacloprid quantities. We optimized the tissue preparation approach for this ELISA on solid samples using peer-reviewed methods29,30,31,32,33,34.
Data collected in experiments were analyzed using Systat 13 (Systat Software Inc., San Jose, CA). Male and female fawn organ concentrations for those fawns that survived versus those that died were compared using t-tests. Our ELISA results indicated that there was contamination of our control group. As a consequence, in addition to ANOVA, ordinary least square (OLS) linear regression was used to assess relationships between imidacloprid concentrations in all organ samples and the response variables birth weight, fawn age, FT3, FT4, jawbone length, and organ weights; alpha was set at 0.05.
Data collected on behavioral observations for adult females and fawns were analyzed separately but combined over observation period (morning and afternoon). Furthermore, we separated deer into three groups (high, moderate, and low) based on organ imidacloprid concentrations. Finally, we used Chi-square tests to determine significant differences among behaviors observed in high, moderate, and low imidacloprid groups for adults and fawns. If Chi-square tests were significant, we used confidence intervals (90%) to assess which behaviors differed among groups (high, moderate, and low).
Doe and Fawn Survival
A total of 24 and 39 fawns was born in 2015 and 2016, respectively. In 2015, 12 of the fawns were born in August and September due to late breeding. Number of single, twin, triplet, and quadruplet litter sizes, respectively, per treatment were 1, 4, 1, 1 (control), 5, 3, 0, 0 (low), 2, 3, 2, 0 (moderate), and 2, 7, 2, 0 (high); 3 fawns were found outside treatment pens and were not included in analyses. Sex ratio (females:males) of fawns was 0.46:0.54 and did not differ by treatment (X23 = 2.98, p = 0.394). In 2016, a control female died and was replaced with another adult female, totaling 21 adult females in our experiment. Fawn and adult female survival decreased over the two field seasons: survival of fawns was 75% and 62% in 2015 and 2016, respectively. Of 20 adult females in 2015, 0% died (100% survival); in 2016, 19% of 21 adult females died (n = 4, 81% survival). Survival of fawns did not differ (p > 0.05) between 2015 and 2016. Additionally, sample size for adult females was too small to evaluate change in survival between the two field seasons.
Imidacloprid Solution Consumption
Water consumption rates in 2015 and 2016 were monitored, and daily consumption was recorded. There were significant interactions in water consumption between treatment and date in 2015 (F15, 436 = 2.22, p = 0.01) and 2016 (F15, 555 = 2.19, p = 0.01). In 2015, when the control was removed from the analysis, date was still significant (F5, 327 = 21.48, p = 0.01) relative to consumption; however, water consumption per adult female was similar across treatments (F2, 327 = 0.60, p = 0.55), indicating the control group consumed significantly more water than the treatment groups. In 2016, when excluding the control group, the high treatment group consumed less water per adult female than the low and moderate groups (F2, 421 = 12.83, p = 0.01), even though consumption of water increased throughout the field season (F5, 421 = 14.25, p = 0.01) (Table 1).
Organ weights were collected from adult females and fawns, and jawbone measurements were collected solely from fawns. Adult females had mean organ weights of 159 ± 8 g for brain, 809 ± 104 g for liver, 388 ± 41 g for spleen, and 87 ± 28 g for genitals. Mean organ weights of fawns were 106 ± 3.9 g for brain, 413 ± 37 g for liver, 102 ± 11.4 g for spleen, and 6 ± 0.9 g for genitals. Female fawn mean organ weights were 96 ± 6 g for brain, 342 ± 55 g for liver, 95 ± 18 g for spleen, and 3 ± 0.6 g for genitals. Male fawn mean organ weights were 115 ± 5 g for brain, 479 ± 48 g for liver, 109 ± 14 g for spleen, and 9 ± 1 g for genitals (Table 2). Average jawbone length results were 13.8 ± 0.4 cm.
ELISA results indicated imidacloprid was found in the control group organs (Table 3), indicating that our treatments were contaminated; there were no significant differences across treatments for liver (F3,18 = 0.511, p = 0.14), brain (F3,18 = 0.058, p = 0.388), genital (F3,18 = 0.17, p = 0.286), or spleen (F3,18 = 0.17, p = 0.328) in adult females, or liver (F3,34 = 0.04, p = 0.943), brain (F3,35 = 0.018, p = 0.576), genital (F3,34 = 0.05, p = 0.707), or spleen (F3,35 = 0.20, p = 0.199) in fawns; gender of fawns was not significant (p > 0.07) in these analyses. However, imidacloprid concentration in spleen samples of adults approached significance (r = 0.36, p = 0.06) when regressed versus control and treatment categories. Nevertheless, this changed our focus from separating ELISA results by treatments to viewing the results relative to concentration of imidacloprid. Mean imidacloprid values in organs for all adult females were 0.42 ± 0.07 ng/g for liver, 0.06 ± 0.05 ng/g for brain, 0.11 ± 0.04 ng/g for spleen, and 0.69 ± 0.05 ng/g for genital (Table 3). Mean imidacloprid values in organs for female fawns were 0.42 ± 0.06 ng/g for liver, 0.03 ± 0.02 ng/g for brain, 0.21 ± 0.05 ng/g for spleen, and 0.26 ± 0.04 ng/g for genital (Table 3). Mean imidacloprid values in organs for male fawns were 0.55 ± 0.07 ng/g for liver, 0.05 ± 0.02 ng/g for brain, 0.19 ± 0.04 ng/g for spleen, and 0.15 ± 0.03 ng/g for genital (Table 3).
Spleen concentrations of imidacloprid were significantly higher (T59 = 2.76, p = 0.007) in fawns that died compared to the fawns that survived. However, an outlier of 1.49 ng/g of spleen tissue was removed from analyses (mean of data with outlier 0.20, range 0–1.49; mean of data without outlier 0.18, range 0–0.91 ng/g of tissue); the revised result also was significant (T58 = 4.36, p < 0.001) (Fig. 1). The fawn with this high spleen imidacloprid concentration survived, which was not consistent with the overall trend in the data. Mean imidacloprid in spleens of fawns that died was 0.33 ± 0.26 ng/g whereas imidacloprid in spleens of fawns that survived averaged 0.10 ± 0.14 ng/g. Birth weight was not correlated with imidacloprid levels in any of the organs evaluated (Table 4). Fawn body weight at death was negatively correlated with imidacloprid levels in the spleen (F1,55 = 8.22, p = 0.005) and genital organs (F1,56 = 4.26, p = 0.04) (Table 4). Fawn age at death was correlated with imidacloprid levels in the spleen (F1,57 = 10.5, p = 0.002) but not in any of the other organs evaluated (Table 4). Adult female FT3 and FT4 values were not correlated with imidacloprid levels in organs (Table 4). Fawn FT3 values were not correlated with imidacloprid concentrations in organs; however, FT4 values in fawns were negatively correlated (F1,39 = 7.48, p = 0.0092, Table 4) with spleen imidacloprid concentrations. Adult female organ weights were negatively correlated with imidacloprid concentrations in genitals (F1,19 = 5.00, p = 0.04) but not with other organ levels evaluated. Fawn organ weights were negatively correlated with spleen (F1,57 = 8.78, p = 0.0044) and genital (F2,54 = 5.55, p = 0.021) (Table 4) imidacloprid concentrations. Fawn jawbone length was negatively correlated with imidacloprid values in the spleen (F1,57 = 9.98, p = 0.002) but not with other organ concentrations (Table 4).
Imidacloprid concentrations in spleen were correlated with fawn survival; therefore, we explored relationships between spleen imidacloprid concentrations and deer behavior. Adult female (n = 21) imidacloprid concentrations in spleen were separated into low (n = 12, range = 0), moderate (n = 4, range 0.056–0.224), and high groups (n = 5, range = 0.248–0.909); the duration of behaviors were compared among groups (all spleens that had 0 ppb concentration were placed in the low group). The low imidacloprid group differed (90% CI) from the high group in the behaviors eat (groups; high = 2.4%, low = 6%), lay (high = 27%, low = 19%), lay/groom (high = 7%, low = 3%), stand/ruminate (high = 1%, low = 2%), run (high = 1%, low = 5%), and stand/groom (high = 8%, low = 5%) indicating that adult deer in the low group had higher activity levels than those in the high group. The moderate group also differed from the low group in the behaviors eat (group; moderate = 10%, low = 6%), lay (moderate = 4%, low = 19%), lay/ruminate (moderate = 2%, low = 5%), stand/ruminate (moderate = 1%, low = 2%), run (moderate = 1%, low = 5%), stand (moderate = 34%, low = 23%), stand/groom (moderate = 13%, low = 5%), and stand/nurse (moderate = 0%, low = 2%); indicating variation in behavior between the two groups (Table 5).
Fawn spleen concentrations of imidacloprid (n = 38) also were placed in low (n = 20, range = 0), moderate (n = 9, range = 0.053–0.121), and high (n = 9, range = 0.148–0.786) groups and the durations of particular behaviors were compared among groups. The low group differed (90% CI) from the high group in the behaviors lay (group; high = 43%, low = 24%), run (high = 0%, low = 4%), stand (high = 16%, low = 22%), stand/groom (high = 2%, low = 6%), and walk (high = 9%, low = 15%); indicating that the high group was less active than the low group. The moderate group also differed from the low group in the behaviors eat (group; moderate = 12%, low = 8%), lay/curl (moderate = 1%, low = 6%), and lay/groom (moderate = 15%, low = 8%); indicating variation in behavior between the two groups (Table 5).
Our study provides the first overview of effects of imidacloprid on white-tailed deer. We documented that deer in our experiment avoided imidacloprid-contaminated water. Moreover, we discovered that fawns that died during our experiment had greater concentrations of imidacloprid in spleens compared to those that survived. Fawns with relatively high concentrations of imidacloprid in spleen and genital organs also tended to be smaller and less healthy than those with relatively low concentrations of imidacloprid in these organs. Finally, our study provides support for reduced activity of adult and fawn white-tailed deer with relatively high concentrations of imidacloprid in spleens.
ELISA results indicated that our control experimental tissues were unintentionally contaminated with imidacloprid. Potential sources of contamination included seed-treated food and vegetation. Deer were fed soy hulls and a corn, oats, and distiller’s mixture ad libitum. Unfortunately, it was unknown if the soybeans and grains fed to our deer were from imidacloprid-treated plants. However, corn and soybeans are commonly (≥94% of U.S. corn, ~50% of U.S. soybeans12) coated with one of the neonicotinoid active ingredients: clothianidin, imidacloprid, or thiamethoxam13. Additionally, deer in our study would often reach through the fence to browse on natural vegetation. The fields adjacent to the captive wildlife facility were a matrix of agricultural crops with a corn field about 50 m north of the facility. It is unknown what pesticides were used on the corn, but it is likely that there was a seed treatment of imidacloprid or clothianidin. In Indiana, neonicotinoid dust was documented to disperse as far as 100 m from the site35. Imidacloprid from fields could be washed off during rain events and be absorbed by other plants, although this transfer is poorly understood19,36. Therefore, uptake of imidacloprid by vegetation adjacent to the facility is a likely source of this contamination.
Water containing imidacloprid was avoided by deer in treatments in our experiment as evidenced by variable concentrations of the neonicotinoid in captive deer. Deer that avoided consumption of treated water likely drank rain water, which was available (up to 0.3 m deep) after storm events during our experiment. Research on cervid avoidance of imidacloprid is unavailable, but avoidance of imidacloprid has been recorded in red-legged partridge (Alectoris rufa) when offered treated seeds37. Other animals detect and avoid toxins in their diets; for example, kudus (Tragelpahus imberbis), impalas (Aepyceros melampus), and goats (Capra aegagrus hircus) in South Africa avoided plants with 5% condensed tannins during the wet season38, likely due to the astringency of these compounds.
Significantly higher concentrations of spleen imidacloprid levels were found in fawns that died compared to those that survived. The spleen produces white blood cells that fight infection and synthesize antibodies39. Imidacloprid can reduce the production of spleen lymphocytes40,41,42, which results in an impaired immune system20. Therefore, immune suppression in our fawns caused by imidacloprid likely was a factor in their deaths. Complimentary results were found in the FT4 values that are a pre-cursor to FT3 hormone, which is instrumental in regulating basal metabolic rate and thermal regulation in deer27. FT4 was inversely correlated with imidacloprid in spleens of fawns. Reduced metabolic rate in fawns with relatively high concentrations of imidacloprid likely explain the lower activity documented in captive deer.
Imidacloprid values in brain were low to undocumented, which was surprising considering that the pesticide affects the central nervous system; we hypothesize that this could be due to an inability of the chemical to cross the blood-brain barrier. The California Environmental Protection Agency found that imidacloprid penetrates the blood-brain barrier. However, Gupta et al.43 found high imidacloprid quantities in rat liver, kidney, lung, and skin, but concentrations in the brain were low. Additionally, Krieger44 noted that the blood-brain barrier in vertebrates blocks access of imidacloprid to the central nervous system, which reduces toxicity.
Fawns had similar birth weights regardless of the level of imidacloprid in their organs. Similarly, in Sprague-Dawley rats, there were no differences in litter size or weight gain in the offspring whether or not mothers were given an intraperitoneal injection of imidacloprid45. Additionally, Gawade41 found no significant difference in weights of imidacloprid exposed Wister rat pups. However, imidacloprid levels in spleen and genital tissues were negatively associated with body weight in fawns at the time of death.
FT3 and FT4 results are indicative of basal metabolic rate and thermoregulation27. Fawn and adult female FT3 values were similar to those reported in other studies, but FT4 results were elevated compared to previous studies27,46,47,48. We do not believe that this was the result of imidacloprid, as this pesticide decreases thyroid function in rats49, Indian wild birds50, and fish51. Rather, the elevated FT4 values may be due to a combination of pregnancy in adult females, the time of year, and artificial feed. Hamr et al.52 found that thyroid hormones of artificially fed deer were elevated compared to deer that consumed natural browse. Additionally, this study also found that hormones were increased in the spring and summer. Bahnak et al.53 documented that pregnant, penned deer have elevated levels of thyroid hormones.
As imidacloprid increased in the spleen, we noted that FT4 levels and spleen size decreased. As stated previously, imidacloprid has been shown to decrease FT4 levels in other vertebrates49,50,51. Additionally, research on rats has shown that organ weights (specifically liver and spleen) decrease as imidacloprid treatment increases54,55,56. From our observations and previous research, we predict that imidacloprid is suppressing the immune function and size of the spleen.
As imidacloprid increased in the genital organs of fawns and adult females, weights of the genital organs decreased. Vohra and Khera56 found that, as oral consumption of imidacloprid increased, the ovaries of lab rats became smaller but the uterus increased in size. Additional research has shown that liver and spleen sizes will decrease as imidacloprid concentration increases; however, there was not an indication that the genital weight decreased54,55,56. Consequently, more research is needed to better understand how imidacloprid and other neonicotinoids affect reproductive tissues in mammals.
Behavioral observations indicated that high concentration of imidacloprid in the spleen resulted in less activity in adult females and fawns. This finding was similar to results on female rats and their offspring that showed significant decreases in grip time as imidacloprid concentrations from intraperitoneal injection increased, an indication of fatigue45. Rat movement was similarly impaired as imidacloprid (via oral consumption) increased55,57.
Samples of liver and spleen organs were collected from white-tailed deer brought to the NDGF Wildlife Health Laboratory for a variety of reasons (e.g., illegal harvest investigations, disease, deer-vehicle collisions) from 2009–2017 throughout North Dakota.; imidacloprid concentrations were evaluated in 367 samples using the same ELISA methods as in our captive experiment. Results indicated that levels of imidacloprid in liver samples were 2.8 times higher in free-ranging deer in North Dakota [average 1.32 (0.10)] than in livers of our captive deer [average 0.46 (0.03)], Table 6. Furthermore, concentrations of imidacloprid in spleen samples from free-ranging deer in North Dakota [0.60 (0.06)] were 3.5 times higher than those in spleens of captive deer [0.17 (0.02), Table 6] in our experiment. Deer exposure to imidacloprid averaged 52.3 ± 4.6% over the years 2009 to 2017. For those free-ranging deer in North Dakota exposed to imidacloprid, average concentrations in spleens increased (r = 0.22, p = 0.002) an average of 0.11 ng/g per year from 2009 to 2017. Furthermore, 77.5% of these deer had imidacloprid levels in spleens equal to or above 0.33 ng/g (i.e., mean level of imidacloprid in spleens of fawns in captivity that died in our experiment). These results indicate that wild populations of deer exposed to imidacloprid are potentially experiencing effects similar to those seen in our captive facility experiment; i.e., reduced activity in adult females and fawns, and specifically in fawns, decreased survival, size, and health. Consequently, additional research is needed to confirm these relationships in free-ranging deer in agricultural landscapes where imidacloprid and other neonicotinoid insecticides are utilized.
Data are available for upload upon the publication of our manuscript.
Goulson, D. An overview of the environmental risks posed by neonicotinoid insecticides. Journal of Applied Ecology 50, 977–987 (2013).
Tomizawa, M. & Yamamoto, I. Binding of neonicotinoids and the related compounds to the insect nicotinic acetylcholine receptor. Journal of Pesticide Science 17, 231–236 (1992).
Buckingham, S., Lapied, B., Corronc, H. & Sattelle, F. Imidacloprid actions on insect neuronal acetylcholine receptors. The Journal of Experimental Biology 200, 2685–2692 (1997).
Matsuda, K. et al. Neonicotinoids: insecticides acting on insect nicotinic acetylcholine receptors. Trends in Pharmacological Sciences 22, 573–580 (2011).
Rose, P. H. Nicotine and the Neonicotidnoids in Mammalian toxicology of insecticides (ed. Marrs, T. C.) 184–220 (Marrs, 2012).
Van Dijk, T. C., Staalduinen, M. A. & Van der Sluijs, J. P. Macro- invertebrate decline in surface water polluted with imidacloprid. Plos One 8, e62374 (2013).
Sánchez-Bayo, F. P., Tennekes, H. A. & Goka, K. Impact of systemic insecticides on organisms and ecosystems in Insecticides-Development of Safer and More Effective Technologies 365–414 (2013).
Tokumato, J. M. et al. Effects of exposure of clothianidin on the reproductive system of male quails. Journal of the Veterinary Medical Science 75, 755–760 (2013).
Douglas, M. R. & Tooker, J. F. Large-Scale Deployment of Seed Treatments has Driven Rapid Increase in Use of Neonicotinoid Insecticides and Preemptive Pest Management in U.S. Field Crops. Environmental Science & Technology 49, 5088–5097 (2015).
Jeschke, P., Nauen, R., Schindler, M. & Elbert, A. Overview of the Status and Global Strategy for Neonicotinoids. Journal of Agricultural and Food Chemistry 59, 2897–2908 (2011).
United States Geological Survey [USGS]. Estimated Annual Agricultural Pesticide Use. Pesticide Use Maps, https://water.usgs.gov/nawqa/pnsp/usage/maps/show_map.php?year=2015&map=IMIDACLOPRID&hilo=L&disp=Imidacloprid (2017).
Stockstad, E. Pesticides under fire for risks to pollinators. Science 340, 674–676 (2013).
Main, A. R. et al. Widespread use and frequent detection of neonicotinoid insecticides in wetlands of Canada’s Prairie Pothole Region. Plos One 9, e101400 (2014).
Seagraves, M. P. & Lundgren, J. G. Effects of neonicitinoid seed treatments on soybean aphid and its natural enemies. Journal of Pest Science 85, 125–132 (2012).
Bredeson, M. M., Reese, R. N. & Lundgren, J. G. The effects of insecticide dose and herbivore density on tri-trophic effects of thiamethoxam in a system involving wheat, aphids, and ladybeetles. Crop Protection 69, 70–76 (2015).
Mason, R., Tennekes, H., Sánchez-Bayo, F. & Jepsen, P. U. Immune Suppression by Neonicotinoid Insecticides at the Root of Global Wildlife Declines. Journal of Environmental Immunology and Toxicology 1, 3–12 (2013).
Maloney, E., Morrissey, C. A., Headley, J. & Peru, K. Cumulative toxicity of neonicotinoid insecticide mixtures to chironomus dilutus under acute exposure scenarios. Environmental Toxicology and Chemistry 9999, 1–11 (2017).
Morrissey, C. A. et al. Neonicotinoid contamination of global surface waters and associated risk to aquatic invertebrates: a review. Environment International 74, 291–303 (2015).
Mogren, C. L. & Lundgren, J. G. Neonicotinoid-contaminated pollinator strips adjacent to cropland reduce honey bee nutritional status. Scientific Reports 6, 29608 (2016).
Gibbons, D., Morrissey, C. & Mineau, P. A review of the direct and indirect effects of neonicotinoids and fipronil on vertebrate wildlife. Environmental Science and Pollution Research 22, 103–118 (2014).
Hoy, J. A., Hoy, R., Seba, D. & Kerstetter, T. H. Genital abnormalities in white-tailed deer in west-central Montana: pesticide exposure as a possible cause. Journal of Environmental Biology 23, 189–197 (2002).
Hoy, J. A., Haas, G. T., Hoy, R. D. & Hallock, P. Observations of brachygnathia superior in wild ruminants in Western Montana, USA. Wildlife Biology in Practice 7, 15–29 (2011).
Zimmerman, T. J., Jenks, J. A., Holler, L. D., Jacques, C. N. & Morlock, W. W. Congenital Hypotrichosis in a white-tailed deer fawn from South Dakota. Journal of Wildlife Diseases 40, 145–149 (2004).
NOAA National Weather Service Cooperator Observer Program. NOAA homepage, http://www.nws.noaa.gov/om/coop/ (2017).
Giorio, C. A. et al. An update of the worldwide integrated assessment (WIA) on systemic insecticides. Part 1: new molecules, metabolism, fate, and transport. Environmental Science and Pollution Research 1–33, https://doi.org/10.1007/s11356-017-0394-3 (2017).
Sikes, R. and the Animal Care and Use Committee of the American Society of Mammologists. Guidelines of the American Society of Mammologists for the use of wild mammals in research and education. Journal of Mammalogy 97, 663–688 (2016).
Bergman, E. J., Doherty, P. F., Bishop, C. J., Wolfe, L. L. & Banulis, B. A. Herbivore body condition response in altered environments: mule deer and habitat management. Plos One 9:e106374, http://journals.plos.org/plosone/article?id=10.1371/journal.pone.0106374 (2014).
Altmann, J. Observational study of behavior: sampling methods. Behavior 49, 227–267 (1974).
Pecenka, J. R. & Lundgren, J. G. Non-target effects of clothianidin on monarch butterflies. Science of Nature 102(3/4), 19 (2015).
Bredeson, M. M. & Lundgren, J. G. The effect of a thiamethoxam seed treatment on pests and yield in cultivated sunflowers. Journal of Economic Entomology 108, 2665–2671 (2015).
Bredeson, M. M., Reese, R. N. & Lundgren, J. G. The effects of insecticide dose and herbivore density on tri-trophic effects of thiamethoxam in a system involving wheat, aphids, and lady beetles. Crop Protection 69, 70–76 (2015).
Mogren, C. L. & Lundgren, J. G. Neonicotinoid-contaminated pollinator strips adjacent to cropland reduce honey bee health. Scientific Reports 6, 29068 (2016).
Pecenka, J. R. & Lundgren, J. G. The importance of dung beetles and insect communities on degradation of cattle dung pats in eastern South Dakota. PeerJ 6, e5220 (2018).
Bredeson, M. M. & Lundgren, J. G. Thiamethoxam seed treatments reduce foliar predator and pollinator populations in sunflowers (Helianthus annuus), and extra-floral nectaries as a route of exposure for seed treatments to affect the predator, Coleomegilla maculate (Coleoptera: Coccinnellidae). Crop Protection 106, 85–92 (2018).
Krupke, C. H., Holland, J. D., Long, E. Y. & Eitzer, B. D. Planting of neonicotinoid-treated maize poses risks for honey bees and other non-target organisms over a wide area without consistent crop yield benefit. Journal of Applied Ecology 54, 1449–1458 (2017).
Bonmatin, J. M. et al. Environmental fate and exposure; neonicotinoids and fipronil. Environmental Science and Pollution Research 22, 35–67 (2015).
Lopez- Antia, A., Ortiz-Santaliestra, M. E. & Mateo, R. Experimental approaches to test pesticide-treated seed avoidance by birds under a simulated diversification of food sources (2014).
Cooper, S. M. & Owen-Smith, N. Condensed tannins deter feeding by browsing ruminants in a South African savanna. Oecologia 67, 142–146 (1985).
Mebius, R. E. & Kraal, G. Structure and function of the spleen. Nature Publishing Group 5, 606–616 (2005).
Mohany, M., Badr, G., Refaat, I. & El-Feki, M. Immunological and histological effects of exposure to imidacloprid insecticide in male albino rats. African Journal of Pharmacy and Pharmacology 5, 2106–2114 (2011).
Gawade, L., Dadarkar, S. S., Husain, R. & Gatne, M. A detailed study of developmental immunotoxicity of imidacloprid in Wistar rats. Food and Chemical Toxicology 51, 61–70 (2013).
Mohany, M., El-Feki, M., Refaat, I., Garraud, O. & Badr, G. Thymoquinone ameliorates the immunological and histological changes induced by exposure to imidacloprid insecticide. The Journal of Toxicological Sciences 37, 1–11 (2012).
Gupta, R. C. & Milatovic, D. Insecticides. Pages 389–407 in R. C. Gupta, editor. Biomarkers in Toxicology. Elsevier Inc. San Diego, California, USA.
Krieger, R. 2010. Hayes’ Handbook of Pesticide Toxicology. Third Edition. Academic Press Cambridge. Massachusetts, USA (2014).
Abou-Donia, M. B. et al. Imidacloprid induces neurobehavioral deficits and increases expression of glial fibrillary acidic protein in the motor cortex and hippocampus in offspring rats following in utero exposure. Journal of Toxicology and Environmental Health 71, 119–30 (2008).
Watkins, B. E., Nachreiner, R. F., Schmitt, S. M., Cooley, T. M. & Ullrey, D. E. Thyroid function in fed and fasted white-tailed deer fawns. Canadian Journal of Zoology 60, 1331–1338 (1981).
Creekmore, T. E. & Creekmore, L. H. Health assessment of white-tailed deer of the Cuyahoga Valley National Recreation Area. U.S. Department of the Interior. Ohio Madison, WI, U.S (1999).
Bishop, C. J., Watkins, B. E., Wolfe, L. L. & White, G. C. Evaluating mule deer body condition using serum thyroid hormone concentrations. The Journal of Wildlife Management 73, 462–467 (2009).
Abbassy, M. A., Marzouk, M. A., Nasr, H. M. & Mansy, A. S. Effect of imidacloprid and tetraconazole on various hematological and biochemical parameters in male albino rats. Journal of Political Sciences & Public Affairs 2, 122, https://doi.org/10.4172/23320761.1000122 (2014).
Pandey, S. P. & Mohanty, B. The neonicotinoid pesticide imidacloprid and the dithiocarbamate fungicide mancozeb disrupt the pituitary–thyroid axis of a wildlife bird. Chemosphere 122, 227–234 (2014).
Priya, P., Maruthi, Y. A. & Chaitanya, D. A. Proceedings of the second International Summit on Integrative Biology. Effect of imidacloprid insecticide stress on levels of serum thyroid hormones and minerals of fresh water fish clarias batrachus (walking cat fish): interaction with cortisol. Hilton-Chicago/Northbrook, Chicago, USA (2014).
Hamr, J. & Bubenik, G. Seasonal thyroid hormone levels of free-ranging white-tailed deer in Ontario. Canadian Journal of Zoology 68, 2174–2180 (2011).
Bahnak, B. R., Holland, J. C., Verme, L. J. & Ozoga, J. J. Seasonal and nutritional influences on growth hormone and thyroid activity in white-tailed deer. The Journal of Wildlife Management 45, 140–147 (1981).
Vohra, P., Khera, K. S. & Sangha, G. K. Physiological, biochemical and histological alterations induced by administration of imidacloprid in female albino rats. Pesticide Biochemistry and Physiology 110, 50–56 (2014).
Memon, S. A., Memon, N., Mal, B., Shaikh, S. A. & Shah, M. A. Histopathological changes in the gonads of male rabbits on exposure to imidacloprid insecticide. Journal of Entomology and Zoology Studies 2, 159–163 (2014).
Vohra, P. & Khera, K. S. Effect of imidacloprid on Reproduction of Female Albino Rats in Three Generation Study. Journal of Veterinary Science & Technology 7, 340, https://doi.org/10.4172/2157-7579.1000340 (2016).
Najafi, G., Razi, M. & Feyzi, S. The effect of chronic exposure with imidacloprid insecticide on fertility in mature male rats. International Journal of Fertility and Sterility 4, 9–16 (2010).
Funding for this study was provided by the South Dakota Agricultural Experiment Station and Federal Aid to Wildlife Restoration (Study No. 3M5842) administered through South Dakota Department of Game, Fish and Parks. Funding for analysis of free-ranging deer in North Dakota was provided by North Dakota Department of Game and Fish. Special thanks to technicians C. Lee, B. Becher, J. Christenson, A. Wieseler, S. Carstens, and J. Jensen at South Dakota State University and R. Herigstad, M. Kietzman, J. Mortenson, H. Prichert, and A. Pachl at North Dakota Game and Fish Department.
The authors declare no competing interests.
Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Berheim, E.H., Jenks, J.A., Lundgren, J.G. et al. Effects of Neonicotinoid Insecticides on Physiology and Reproductive Characteristics of Captive Female and Fawn White-tailed Deer. Sci Rep 9, 4534 (2019). https://doi.org/10.1038/s41598-019-40994-9
This article is cited by
Simultaneous Determination of Neonicotinoid Insecticides and Metabolites Residues in Milk and Infant Formula Milk Powder by EMR-Liquid Chromatography-Tandem Mass Spectrometry
Food Analytical Methods (2023)
Development of an isotope dilution liquid chromatography/tandem mass spectrometry method for the accurate determination of neonicotinoid pesticides, imidacloprid, clothianidin, and thiamethoxam in kimchi cabbage reference materials
Journal of Analytical Science and Technology (2022)
The Effect of Neonicotinoids Exposure on Oreochromis niloticus Histopathological Alterations and Genotoxicity
Bulletin of Environmental Contamination and Toxicology (2022)
Seed treatments containing neonicotinoids and fungicides reduce aquatic insect richness and abundance in midwestern USA–managed floodplain wetlands
Environmental Science and Pollution Research (2022)
Archives of Toxicology (2022)