Skip to main content
Browse Subject Areas

Click through the PLOS taxonomy to find articles in your field.

For more information about PLOS Subject Areas, click here.

  • Loading metrics

Neonicotinoid Insecticide Residues in Surface Water and Soil Associated with Commercial Maize (Corn) Fields in Southwestern Ontario

  • Arthur Schaafsma ,

    Affiliation Department of Plant Agriculture, University of Guelph, Ridgetown Campus, Ridgetown, ON, Canada

  • Victor Limay-Rios,

    Affiliation Department of Plant Agriculture, University of Guelph, Ridgetown Campus, Ridgetown, ON, Canada

  • Tracey Baute,

    Affiliation Ontario Ministry of Agriculture Food and Rural Affairs, Ridgetown, ON, Canada

  • Jocelyn Smith,

    Affiliation Department of Plant Agriculture, University of Guelph, Ridgetown Campus, Ridgetown, ON, Canada

  • Yingen Xue

    Affiliation Department of Plant Agriculture, University of Guelph, Ridgetown Campus, Ridgetown, ON, Canada


Neonicotinoid insecticides have come under scrutiny for their potential unintended effects on non-target organisms, particularly pollinators in agro-ecosystems. As part of a larger study of neonicotinoid residues associated with maize (corn) production, 76 water samples within or around the perimeter of 18 commercial maize fields and neighbouring apiaries were collected in 5 maize-producing counties of southwestern Ontario. Residues of clothianidin (mean = 2.28, max. = 43.60 ng/mL) and thiamethoxam (mean = 1.12, max. = 16.50 ng/mL) were detected in 100 and 98.7% of the water samples tested, respectively. The concentration of total neonicotinoid residues in water within maize fields increased six-fold during the first five weeks after planting, and returned to pre-plant levels seven weeks after planting. However, concentrations in water sampled from outside the fields were similar throughout the sampling period. Soil samples from the top 5 cm of the soil profile were also collected in these fields before and immediately following planting. The mean total neonicotinoid residue was 4.02 (range 0.07 to 20.30) ng/g, for samples taken before planting, and 9.94 (range 0.53 to 38.98) ng/g, for those taken immediately after planting. Two soil samples collected from within an conservation area contained detectable (0.03 and 0.11 ng/g) concentrations of clothianidin. Of three drifted snow samples taken, the drift stratum containing the most wind-scoured soil had 0.16 and 0.20 ng/mL mainly clothianidin in the melted snow. The concentration was at the limit of detection (0.02 ng/mL) taken across the entire vertical profile. With the exception of one sample, water samples tested had concentrations below those reported to have acute, chronic or sublethal effects to honey bees. Our results suggest that neonicotinoids may move off-target by wind erosion of contaminated soil. These results are informative to risk assessment models for other non-target species in maize agro-ecosytems.


Neonicotinoids are a class of systemic insecticides, which are absorbed and translocated throughout the plant and provide in-plant protection from pests for a period during plant establishment [1]. The neonicotinoid class of insecticides were adopted to replace older carbamate and organophosphate chemistries considered to be more hazardous to applicators and other non-target organisms particularly mammals [2]. Neonicotinoids may be applied as seed treatments, foliar sprays, soil drenches, granules, injection or through—irrigation systems [2]. The variety of methods for their application, along with their systemic properties and low toxicity to mammalian vertebrates has resulted in wide-spread adoption for crop protection [2,3]. In particular, their convenience as seed treatments has resulted in a shift from their prescriptive use in response to pest scouting, to prophylactic use as insurance against pest damage [3]. Currently-seven neonicotinoids, clothianidin, imidacloprid, thiamethoxam, dinotefuran, acetamiprid, thiacloprid and nitenpyram, are used in agricultural production [4]. Imidacloprid was the first neonicotinoid registered on field crops in Canada in 2001 [5]. Presently, three of these, clothianidin, thiamethoxam and imidacloprid are registered for use on almost all major field crops in Canada. Clothianidin and thiamethoxam are the neonicotinoids most commonly used in southwestern Ontario. This group of insecticides dominates the seed treatment market in Ontario—with over 99% of maize (corn), 60–80% of soybean, 95% of dry bean, 25% of winter wheat and 100% of canola crop areas planted with a neonicotinoid seed treatment in 2013 [5].

Pollinator Colony Collapse Disorder (CCD) is a major issue facing apiculture globally [613]. Many interacting and confounding factors are debated to cause honey bee (Apis mellifera L.) decline, including parasites, disease, pesticide exposure, habitat loss, and climate change, with no single factor standing out as the primary cause [8,1424]. Historically most acute bee poisonings arising from pesticide use have occurred from exposure to broadcast applications of insecticides on plants on which bees are foraging [25]. Recently, coincident with the widespread adoption of neonicotinoid insecticides as seed dressings for field crops and the introduction of pneumatic maize planters, acute bee mortality near planting time has been observed in Europe [2631], the United States [32] and in Canada [33,34]. This has been attributed to exposure to neonicotinoid insecticide residues escaping from the planter’s vacuum exhaust [3,3338]. Besides direct exposure to flying bees, these residues have the potential to contaminate flowers, pollen or other resources used by bees [32]. Neonicotinoid residues have been found in fresh pollen of plants [32,3941], bee-collected pollen [–29,32,33,42], nectar [41], plant guttation fluid [43,44], and planter exhaust dust [2632]. Neonicotinoid insecticides are water-soluble, making them candidates for surface water contamination [4548] and have been shown to be persistent in water and soil under some environmental conditions [49].

Honey bees collect water for several purposes: to thermo-regulate their nest by evaporative cooling [–50], to dilute stored honey and glandular secretions to feed brood, and to maintain humidity in their nests for larval development [51]. Water is collected by individual foragers with some specialized to this task for long periods [52]. Water foraging bees can collect 44 μL of water/bee for each water-collecting flight [53]. Each bee in a group of 200 consumes about 11 μL of water daily at 35°C [54]. Neonicotinoid residues in surface water may also affect aquatic invertebrates and ecosystem health [4547,55]. Currently there are only limited data available on neonicotinoid residues in water sources related to commercial maize production that may be used by honey bees, except a recent report of neonicotinoids detected in streams of an area of intense corn and soybean production of Midwestern United States [56]. We hypothesized that neonicotinoid residues occurring in water sources within and in close proximity to commercial maize fields are a source of exposure to honey bees. Our objective was to investigate the quantity, distribution and temporal dynamics of clothianidin and thiamethoxam in surface water related to maize production, as one consideration to inform the risk assessment of acute and chronic exposure of honey bees to neonicotinoid insecticide residues. Melted snow in the spring in Canada is also an important water source around agricultural fields. The average annual precipitation from 1981 to 2010 for the five counties where our sites are located (Essex, Chatham- Kent, Lambton, Middlesex and Elgin) ranged from 878 to 1012 mm. Average annual snowfall ranged from 79 to 166 mm as rainfall equivalent, which accounted for 9–16% of the average annual precipitation, respectively [57]. We have observed that drifted snow often contains soil scoured from fields during high winds and we hypothesized these soil residues could be contaminated by neonicotinoid insecticides possibly contributing to detectable residues in standing water around fields. For this study a fully validated liquid chromatography/tandem mass spectrometry (LCMS/MS) method is described for the simultaneous analysis of clothianidin and thiamethoxam in soil and water.

Materials and Methods

Ethics statement

These field studies did not involve endangered or protected species. No specific permits were required to access the field study sights and all were privately owned by cooperators for agricultural crop production, and visited by permission. Permission was obtained by Tracey Baute, Provincial Entomologist, Ontario Ministry of Agriculture Food and Rural Affairs. Under privacy law we are unable to publicly disclose the names or contact information of the cooperators without their permission. We have all this on record and access can be requested for verification or additional work in future by contacting Tracey by email (

Chemicals and reagents

Certified clothianidin and thiamethoxam standards and their respective deuterium-labeled internal standard (clothianidin-d3 and thiamethoxam-d3) were obtained from Sigma-Aldrich (St. Louis, MO, USA; Pestanal class, purity ≥99.5%). LCMS grade methanol was obtained from JT Baker (Phillipsburg, NJ, USA). LCMS grade water and acetonitrile were obtained from OmniSolv (Billerica, MA, USA). Anhydrous magnesium sulfate and sodium chloride, sodium citrate tribasic dehydrate and sodium hydrogencitrate sesquihydrate were obtained from Sigma-Aldrich. N-hexane and formic acid were purchased from Acros Organics (Geel, Belgium, part of Thermo Fisher Scientific Inc.). Stock solutions were prepared by dissolving clothianidin and thiamethoxam standards to 1mg/mL and their respective deuterated internal standard to 100 ug/ml in acetonitrile in amber glass flasks. Mixed working standard solutions were prepared for these two neonicotinoids at 10 ng/ml and 100 ng/ml and their respective internal standard at 100 ng/ml in 1:1 methanol/water with 5mM formic acid. All solutions were stored in darkness at 2°C.

Experimental fields

As part of a larger study on honey bee exposure to neonicotinoid residues in maize fields, we enlisted nine farm cooperators, each contributing 2 commercial maize fields (minimum 20 ha in size, most 40 ha or larger), with both fields paired with one apiary within a 3-km radius of both fields. Each cooperator was located in one of 5 counties (Essex, Chatham- Kent, Lambton, Middlesex and Elgin) in southwestern Ontario (Fig. 1). Field characteristics are given in Table 1 and their GPS locations can be found in the S1 Table).

Fig 1. Map of subject field locations in 2013 (modified from the original by Cartographic Office, Department of Geography, University of Guelph).

1–9: maize fields and bee yards; 10: fields for snow drift samples; 11: blank soil taken.

Table 1. Soil texture class and crop rotation and tillage history of subject maize (corn) fields.

Sample collection

Sample fields and apiaries were surveyed weekly from 29 April to 28 June 2013 for water sources that bees could potentially visit. Field samples were categorized as being from “within” or “outside” of the subject fields where “within” field samples were collected from puddles of standing water within the perimeter of the field and “outside” samples were collected from puddles, ditches or field drainage outlets from within 0 to 100 m of the field perimeter. At apiaries numbered 1, 4, 5, and 7 puddles were sampled within 100 m from the beehives and water collected at apiary 9 was from a pond (10 m in diameter) within 10 m of the beehives. No water samples were found for collection at apiaries numbered 2, 3, 6, or 8. If multiple water samples of the same type (e.g. puddles within field) were collected from a field within the same sampling period these were considered repeated measures in space. However, it should be noted that the subject fields were large and that when multiple samples were taken from the same field, they were from different parts of these fields and most likely had different characteristics from one another. Approximately 100 ml of water was collected for each sample in a new 100 ml amber HDPE bottle (Fisher Scientific, Ottawa, ON) using a new 50 ml disposable syringe (Fisher Scientific, Ottawa, ON), placed in a cooler with freezer packs in until returned to the laboratory by the end of each sampling day to be stored at -20°C in complete darkness until analyzed using LC-MS/MS.

On the day of planting, soil grab samples were taken from the top 5 cm of the surface (representing the depth of seed placement zone) immediately before and immediately after planting. Ten subsamples were taken at random within each field, while walking in an M pattern across the field; sub-samples taken after planting were collected from the mid-point between two newly planted rows to avoid the width of the placement zone of treated seeds. Subsamples were obtained from conventionally tilled fields by scooping the appropriate amount by a hand that was protected by a virgin disposable nitrile glove (Fisher Scientific, Ottawa, ON) or from no-till fields using a disposable 100 mm × 15 mm Petri dish (Fisher Scientific, Ottawa, ON) where the surface soil was previously undisturbed. Each subsample was approximately 100 g; subsamples were pooled directly into a new plastic bag that was then placed into another plastic bag, and mixed thoroughly in the field. The sample was placed immediately into a dark picnic cooler containing freezer packs for transport back to the laboratory, followed by immediate dark and frozen storage (-20°C) until analysis.

Two samples of top soil (0–10 cm deep, 2 kg each) were collected from an old growth Carolinian forest located at Clear Creek Forest near Clearville, ON, approximately 0.5 km from the nearest surrounding agricultural land, to provide soil of the region for use as a blank sample for analytical method validation.

As an unplanned and preliminary study to determine if drifting snow is a potential contributor to off-site neonicotinoid residues, we took the opportunity to sample two snow drifts each located on the leeward side of two adjacent 40-ha fields near Ridgetown, ON. These two fields are typical in soil type and cropping practice of those found in the region, and occur somewhat central to region where the water samples were taken. A series of small to moderate snow events, (3–10 cm) each accompanied by high winds, occurring on frozen bare soil, resulted in large snow drifts on the edge of these two fields in January. Conveniently, these fields were similar in size, soil type, topography, cropping history, and history of neonicotinoid use. The leeward field had been tilled in the autumn and left bare, while the windward field had been planted with winter wheat without tillage. There were obvious alternating strata of clean and soiled snow in the drift profile.

The first sample was collected on 27 January in the windward field from a snow drift approximately 2 m in height and 3 m wide at the base located along the center of the eastern edge. This first sample was a composite of numerous small sub-samples, taken randomly through the vertical profile of the drift on 27 January to see if neonicotinoid residues could be detected. This field had a crop history of wheat in 2011 followed by maize in 2012 and soybeans in 2013, and had a variable soil type and topography. Winter wheat was planted again in the fall of 2013 with no tillage. All of the seed for these crops was treated with a neonicotinoid insecticide at the lowest recommended rate for each crop. All samples were taken with a snow shovel that had been cleaned by thoroughly scrubbing with the visibly cleanest snow from the drift the sample was to be taken from. After neonic residues were confirmed in this first sample, the second two samples were taken on 30 January, each consisting of a 0.027-m3 snow cube one from the same drift as for 27 January and the second taken from a similar drift with similar dimensions on the leeward side of the neighbouring field across the road to the east. For each drift a vertical face was dug out to the ground level to expose the layers of drifted snow. A single sample was taken from the thickest layer of soiled snow in the drift from each field. We selected the same layer from each drift assuming they were deposited during the same drifting event. These samples were collected inside a new black plastic bag fit into a bucket, taken immediately to the laboratory and allowed to melt in darkness at room temperature for 48 h before extraction. There was no replication.

Neonicotinoid extraction

Clothianidin and thiamethoxam were extracted using the QuEChERS (quick, easy, cheap, rugged and safe) procedure [58] without a solid phase extraction [59] by placing 10 ml of water or melted snow or 10 g of soil into a 50 mL polypropylene disposable centrifuge tube, adding 20 mL acetonitrile, vortexing for 1 min followed by addition of 4 g magnesium sulphate, 1 g sodium chloride, 1 g sodium citrate tribasic (SCT) and 0.5 g sodium hydrogencitrate sesquihydrate (SHS) and shaking thoroughly for 1min. Each sample was then centrifuged for 5 min at 3000 rpm in a table-top Thermo IEC Central CL2 centrifuge (Milford, MA, USA). A 4-mL aliquot of the resulting acetonitrile supernatant was transferred to a 5 mL glass test tube containing 20 μL of 100 ng/ml mix internal standard solution followed by evaporation to dryness using a Pierce Reacti-Therm III heating module (Rockford, IL, USA) at 40°C under gentle filtered air stream in darkness. The final residue was reconstituted in 1 mL of 1:1 methanol/water (v/v) containing 5 mM formic acid (dilution solvent), vortexed for 2 min and transferred to a 2 mL amber glass auto-sampler vial for LC-MS/MS analysis. Moisture content was determined by oven drying soil samples until weight stabilized, and comparing the dry versus wet mass. Concentration in soil was corrected and expressed in terms of dry soil mass. Melted snow samples were poured into 10 L autoclavable polypropylene storage bottles and homogenized over 5 min using a magnetic stir bar. A total of 4 subsamples were collected into 250 mL new Nalgene bottles under continuous stirring. All snow samples were analysed within 48 hr of collection using a 10 mL aliquot of each subsample giving a total of four replicates per sample.

LC-MS/MS detection

Clothianidin and thiamethoxam determinations were made by injecting a 50 μL aliquot of extract into a 150 mm Gemini C18 reverse phase column (Phenomenex, Torrance, CA) with an Agilent 1100 Series HPLC (Agilent Technologies, Santa Clara, CA, USA). The peak off the HPLC was introduced to an Ionics EP 10+ modified API 365 triple quadruple mass spectrometer (AB SCIEX, Concord, ON) system equipped with an electrospray ionization source (ESI-MS/MS). The chromatographic separation was performed using a gradient program (25 min) with a binary mobile phase consisting of A (methanol and 5 mM formic acid) and B (water and 5 mM formic acid) at a flow-rate of 1 mL/min [60]. The source gas temperature was set to 550°C, nitrogen curtain gas 80 psi, nebulizer gas 8, collision gas 2, and ionization voltage 5000 V. Nitrogen gas was produced by a dedicated Parker Balston Source LCMS-5000 Tri Gas Generator (purity > 99%) and was used as the curtain, drying and collision gases (Haverhill, MA, USA). The gradient began with 25% A and ramped linearly over 15 min to 95% A, these conditions were held for 4 min and finally for a 6 min equilibration for resetting to initial conditions of 25% A. All parameters used in the detection and quantitation were obtained via direct infusion of individual analytes (10 ng/μL solutions in 1:1 methanol/water with 5 mM formic acid) into the ESI-MS/MS at 10 μL/min using a Fusion 100 infusion pump (Chemyx Inc, Stafford, TX, USA) fitted with a 500 μL Gastight 1750 syringe (Hamilton, Reno, NV, USA). Each compound was analysed in positive ion polarity mode using a multiple reaction monitoring (MRM) procedure with one precursor ion (Q1) and two product ions (Q3). The most intense peak in Q3 was used for quantification (quantifier ion) and the second peak for confirmation (qualifier ion). MRM parameters were optimized by selecting collision energy and de-clustering, focusing and cell exit potentials producing the most intense response of the precursor and product ions for each corresponding analyte (Table 2). MRM transitions obtained for clothianidin, thiamethoxam and clothianidin-d3 were in agreement with values reported by Tanner and Czerwenka [60], while transitions found for thiamethoxam-d3 were 295.1 m/z for Q1, and 184.1 and 214.1 m/z for Q3 (Table 2).

Table 2. Optimized multiple-reaction monitoring (MRM) conditions used for the LC-ESI-MS/MS analysis of clothianidin, thiamethoxam and their respective deuterium-labeled internal standards (IS).

For soil analyses, blank samples used in the recovery and calibration experiments were obtained as described previously. Each sample was divided into 3 subsamples and analysed separately for the presence of the target compounds. The subsample with the lowest concentration of clothianidin was used as the blank matrix. For analysis of water and melted snow, filtered municipal well water was used for blank samples. Recovery tests were performed in triplicate by spiking homogenized 5 g soil or 5 ml water blank samples with the appropriate volume of analytical standards at three concentrations; 0.10, 1.00 and 10.00 ng/g for soil; and 0.05, 0.50 and 5.00 ng/ml for water. Spiked samples were left to equilibrate for 3 d at 40°C in darkness followed by a standard extraction procedure and analysis. In this study, to compensate for variation of signal intensities due to matrix effect [61] commercially available deuterium analogs (clothianidin-d3 and thiamethoxam-d3) were used as stable isotopically labeled internal standards (IS, Fig. 2). Clothianidin and thiamethoxam concentrations were determined using matrix-matched calibration curves at 9 concentrations from 0.06 to 4.00 ng/mL in addition to a double blank (matrix extract) and a blank (matrix extract with their corresponding IS) sample.

Fig 2. LC-ESI (+)-MS/MS MRM chromatograms of a soil sample spiked with 0.04 ng/g of clothianidin and thiamethoxam and 1 ng/g clothianidin-d3 and thiamethoxam-d3 internal standards.

LC-ESI-MS/MS system control, data acquisition, processing, peak-area integration, linear regression and final quantification were performed using Analyst 1.4.1 software (AB Sciex, Concord, ON). The linearity of the calibration curve was determined from the linear regression analysis of the peak area (height) ratios of analyte/IS versus analyte concentrations. Detection and quantification limits (LOD and LOQ) were based on estimating the contribution of the background noise signal found in the blank matrix extract. LOD and LOQ were calculated as the mean peak height (n = 4) that can be detected with reasonable certainty using the mean height of the noise signal plus 3 and 10 times standard deviation, respectively [62].

Soil samples collected from Clear Creek Forest and snow drift samples were analysed further for an additional 5 neonicotinoids (imidacloprid, thiacloprid, acetamprid, dinotefuran and nitempyram) and 3 herbicides (metolachlor, atrazine and imazethapyr) using the method described above. LOD, LOQ and average percentage of recovery of 3 spiked samples prepared in triplicate (0.10, 1.00 and 10.00 ng/g) are shown in Tables 3 and 4 for soil dry weight and melted snow, respectively.

Table 3. Determination of 7 neonicotinoids and 3 herbicide residues (ng/g; dry weight) using QuEChERS sample preparation and LC-ESI(+)-MS/MS analysis of two soil samples collected from a conservation forest of old growth Carolinian species.

Table 4. Determination of 7 neonicotinoids and 3 herbicide residues (ng/ml of melted snow) using QuEChERS sample preparation and LC-ESI(+)-MS/MS analysis in three snow drift samples collected in January 2014 from the edge of two harvested maize fields near Ridgetown, ON (mean of four subsamples).

Analytical performance

The validated LC-ESI-MS/MS method for simultaneous detection of both compounds showed good linearity for calibration curves (r >0.989) (Table 5) and repeatability expressed as relative standard deviations (<15%). LOD and LOQ were 0.017 and 0.037 ng/mL in water and 0.023 and 0.063 ng/g in soil, respectively, for clothianidin and 0.004 and 0.011 ng/mL in water and 0.017 and 0.045 ng/g in soil, respectively, for thiamethoxam. Mean recovery for all spiked samples was 92% and 112.9% for clothianidin and 89.2% and 90.8% for thiamethoxam in water and soil, respectively. Higher recovery rates for clothianidin were observed in the sample with the lowest spiked amount in soil due to a chromatographic peak from target compound found in the blank. All values were corrected for the recovery rate of each compound.

Table 5. Linearity of calibration curves, limits of detection and quantification, and recovery at 3 spiked levels of clothianidin and thiamethoxam in water (ng/ml) and soil (ng/g) samples.

Statistical analysis

Because clothianidin and thiamethoxam are the neonicotinoids used most commonly in southwestern Ontario, and clothianidin is a metabolite of thiamethoxam, we report the total quantity of clothianidin and thiamethoxam to represent the neonicotinoid residue, except when specifically noted. All statistical analyses were performed using SAS v. 9.4 (SAS Institute, Cary, NC). Water samples collected from “within”, “outside”, or from apiaries were grouped into four discrete sampling periods (Pre-plant (1–2 weeks before planting), 1–3, 4–5, and 6–7 weeks post-planting) to accommodate variations in sampling dates and differences in rainfall events at different locations and to allow comparisons of residues before and after fields were recharged with new neonicotinoid applications. The total neonicotinoid concentration in water data was subjected to log10 transformation to meet the assumptions of analysis of variance. Differences between the water sampling categories within each sampling period were analyzed using PROC MIXED with repeated measures where sample location (“inside”/”outside”/”apiary”) was the fixed effect, field was a random effect, and sample category was the repeated measure sampled from subject field. To ensure that assumptions of normally distributed residuals and homogeneous error variance were met, PROC UNIVARIATE was used to test residuals. The Shapiro-Wilk statistic was used to test residuals for normal distribution and studentized residuals were calculated to test for outliers. The α level for statistical significance was set at 0.05 for all analyses. For the analysis of neonicotinoid concentration in soil data were subjected to log10 transformation to meet the assumptions of normal distribution. Again PROC MIXED was used to test the differences in neonicotinoid concentrations in soil with sampling period (pre- or post-plant) as a fixed effect and field as a random effect. PROC CORR was used to test the correlation between the total neonicotinoid concentration in soil and in standing water within fields.


Neonicotinoid residues in water

The mean (± SE) neonicotinoid concentration measured in water samples is presented in Table 6. Clothianidin was detected above the LOD in 100% of the 76 samples collected during the 9week sampling period and thiamethoxam was detected in 98.7% (75 out of 76) of the samples. Clothianidin residues were generally higher than those for thiamethoxam (maximum of 43.60 versus 16.50 ng/mL, and mean of 2.28 versus 1.12 ng/mL, for clothianidin and thiamethoxam, respectively).

Table 6. Mean (± SE) of total1neonicotinoid concentration (ng/mL) measured in water sampled within or in close proximity (≤ 100 m) of maize fields before and after planting in Ontario in 2013.

Of the 76 water samples taken, 86.8% (66 out of 76) of the samples had total neonicotinoid residue concentrations lower than 5 ng/mL, 6.3% (4 out of 76) of samples had concentrations between 5 and 10 ng/mL, and 7.9% (6 out of 76) of samples above 10 ng/mL. The highest total neonicotinoid concentration measured was 44.38 ng/mL from a puddle within the field in week 4–5 after planting (Fig. 3). The highest total neonicotinoid concentration measured in puddle outside the field, ditch and drain was 17.83, 12.25 and 6.21 ng/mL, respectively.

Fig 3. Scatter distribution and notched boxplot of water samples collected from the puddles within/around commercial maize fields, ON, 2013.

(1Total of clothianidin and thiamethoxam).

Temporal dynamics of residues in water

For water collected from within maize fields, total neonicotinoid concentration increased sharply after maize planting. The concentration in water during weeks 1–3 and weeks 4–5 after planting was 4.6 times higher and 5.9 times, respectively, higher compared with weeks 1–2 before planting (Fig. 4). The concentration in water decreased at weeks 6–7 after plant, and returned to values similar to those measured at the beginning of the sampling period. In contrast, for water samples collected outside of the maize fields, neonicotinoid residues remained constant during the 9-wk period. The concentrations of total neonicotinoids in water sampled from puddles within fields in weeks 1–3, and weeks 4–5 after planting tended to be higher than those collected during the same period from around the field (weeks 1–3, p = 0.0861; weeks 4–5, p = 0.0572) (Table 7).

Fig 4. Temporal values of total neonicotinoid concentration (± SEM) for water collected within maize fields compared to samples collected from the puddles outside but in close proximity to these fields.

Different letters indicate significant differences in mean neonicotinoid concentration between sampling periods for water sampled within field. (SAS PROC mixed PDIFF, p = 0.05). (1Total of clothianidin and thiamethoxam).

Table 7. Comparison of total1 neonicotinoid concentration between puddles of standing water within and those outside maize fields collected in the same sampling period.

Neonicotinoid concentrations in soil

Multi-residue analysis of the two soil samples collected to provide analytical blanks from the conservation forest each revealed detectable clothianidin (mean 0.03 and 0.11 ng/g), but no thiamethoxam (Table 3). One of the samples contained imidacloprid at the limit of detection (0.01 ng/g). Both samples also contained residues of the herbicide atrazine commonly used in maize fields.

The mean neonicotinoid concentration found in the soil sampled to the 5 cm depth within fields after planting was approximately 2.5 times that found in soil sampled immediately before planting (F = 9.00, df1 = 1, df2 = 17, p = 0.008) (Fig. 5). There were no significant correlations found between soil concentration of neonicotinoid residues determined before or after planting and subsequent concentrations determined in surface water for samples collected within maize fields (Table 8).

Fig 5. Concentration (± SEM) of neonicotinoid residues in soils, sampled from commercial maize fields, taken pre- and post-planting in ON, 2013.

Bars with different letters are significantly different (SAS PROC mixed PDIFF, p = 0.05). (1Total of clothianidin and thiamethoxam).

Table 8. Correlation between total1 neonicotinoid concentration in surface soil and standing water within fields.

Neonicotinoid insecticides in drifted snow banks around maize fields

For the composite sample taken from the entire vertical profile of the first snow drift, the concentration of all neonicotinoids analysed in the melted snow was below or at the detection limit except for traces of thiacloprid (0.01 ng/mL) (Table 4). Quantifiable residues of clothianidin (0.16 and 0.20 ng/mL) were found in samples taken from the drift stratum containing the most wind-scoured soil as determined visually. Quantifiable levels of the herbicides atrazine and metolachlor were also found in all samples.


These data were collected in a crop season typical of the region. All water samples contained detectable levels of neonicotinoid residues. Water samples collected from within maize fields had higher concentrations than those collected from outside the fields after planting (marginally). While we only sampled during the period from 1–2 weeks before to approximately 7 weeks after planting, neonicotinoid concentrations in water samples from within fields were comparable to those outside fields before planting. They were greater for up to 5 weeks after soils were recharged with insecticide after planting, and then comparable thereafter. For samples collected from within maize fields, only 4 had neonicotinoid concentrations higher than 10 ng/mL. All of these were taken from standing puddles within fields between 1–6 wk after planting following a heavy rain event. The 3 samples with the highest concentrations (15–44 ng/mL) were all from standing puddles associated with post-planting rain events within maize fields taken between 1 and 4 weeks after planting. These results suggest that the greatest exposure for non-target organisms to neonicotinoid residues in water within maize fields occurred during the first 5 weeks after planting and most often after a rain event.

We consider four main sources for neonicotinoid residues contaminating puddles within maize fields: carryover soil residues from previous applications, spilled seed, planted seed, and contaminated fugitive planter dust on the soil surface. Regarding carryover, soil samples collected in the field before planting contained similar levels of carryover residues as the levels of residues measured in the water. This was true for water collected within and outside of the fields before planting, suggesting that soil residue levels might be predictive of those in surface water in and around maize fields before and after the sampling period. However we found no correlation between levels found in water to those found in soil during the period of sampling, with the exception of a few fields that had a higher rate of insecticide introduced either by application rate on the seed or due to replanting; water samples from these fields tended to have higher neonicotinoid concentrations. These data may suggest a more-or-less equilibrium state of association between residues in the soil and those in water in contact with this soil for most of the year. A spike in contamination occurred after soils were re-charged with new insecticide at planting. The most acute source of contamination would likely be puddles forming in areas of the field where treated seeds were spilled and remain on the surface. Goulson [63] reports these exposed seeds as potential sources for acute bird toxicity and birds are much more sensitive to neonicotinoids than most invertebrates. The agricultural industry and regulatory agencies are aware of this exposure risk and require that best management practices be followed to minimize this risk, however continued vigilance is required to minimize the occurrence of exposed treated seed on the soil surface [6466]. Vacuum-planter exhaust dust [33] after it settles on the soil surface is another potential source for surface water contamination. We measured approximately 1 ng/cm2 of total neonicotinoid active ingredient settling on soil surfaces during planting of treated maize using vacuum planters in our own field experiments (data not shown). We also measured 2.5 times the amount of neonicotinoid residues in soil grab samples taken immediately before compared with immediately following planting. These were randomly taken, while avoiding newly seeded rows suggesting that the increase in insecticide residues at the soil surface was a direct result of corn planting, including dust from planter exhaust, large abraded seed treatment particles from seed outlet and from other openings of the planter. Finally, the direct contribution after planting to residues in surface water from insecticide on the seeds is uncertain. Conceivably this could be the largest single source of neonicotinoids to contaminate surface water within fields of maize shortly after planting but little is known about their movement in the soil profile during this period.

Neonicotinoid concentrations (2.41 ng/mL) in water samples collected from around maize fields were approximately 13 fold greater than the mean level of 0.185 ng/g for total neonicotinoids reported for water from wetlands of the Canada Prairie pothole region associated with canola production during the crop growing period [47]. The two regions differ substantially in climate, agronomy and size. The prairies have colder winters, generally less rainfall, and cultivate more canola and small grains in rotation than in Ontario. Therefore neonicotinoid insecticides are used less frequently in the rotation, and mainly for canola production. In contrast, Ontario, where maize is produced, is a region experiencing warmer winters, more precipitation, and more frequent use of neonicotinoid seed treatments on several crops in addition to maize. Our results were also much higher than the maximum 0.257 ng/mL for clothianidin and 0.185 ng/mL for thiamethoxam detected in streams in a high corn and soybean producing region in the United States [56]. We suggest that our samples were taken closer to the time and place of application and subject to much less dilution and movement. Spray drift, surface or subsurface movement of water [67] and perhaps wind movement of treated seeds [47] contribute to the movement of neonicotinoid residues from farmland into waters. Our results support that wind erosion of contaminated soil is a potential contributor to off-target residues in soil [68] and water [47]. We believe our data from snow drifts, and from a non-agricultural soil, combined with the detection of common agricultural herbicides, which are persistent and also known to move in soil dust [69], collectively support this proposal.

Bees often use standing water as a foraging resource, and can collect 44 mg (approximately 44μL) of water during each water-collecting flight [53]. For our worst case, (44.38 ng/mL in a puddle of water in a treated maize field shortly after planting following a rain event), each water foraging bee could collect up to 1.95 ng of neonicotinoid active ingredient in one flight. Similarly if, a bee consumed about 11 μL of water daily at 35°C [54], it could consume up to 0.49 ng of neonicotinoid daily, if that was the only water available. These values are about ten-fold less than the acute oral LD50s of 3.8 and 5.0 ng/bee reported for honey bee, for clothianidin and thiamethoxam, respectively [35,36]. In addition, we do not know what portion this water might contribute to the total consumed or collected by a honey bee. The majority of water samples tested, whether originating from within or from outside maize fields, had concentrations less than 5 ng/mL, about 100 fold less than the acute oral LD50 used in the example above. These data suggest that standing water in and around the commercial fields of maize were unlikely contributors to acute toxicity to honey bees.

Sublethal effects of neonicotinoid insecticides on non-target species are the subject of much speculation [70,71]. However, for honey bees, the chronic (10 days) no observed effect concentration (NOEC) of clothianidin, thiamethoxam and imidacloprid is in the order of 10 ng/g [3537,72]. The NOEC of imidacloprid to bumble bees was <2.5 ng/g for reproduction [72]. A sublethal dose of thiamethoxam at 1.34 ng/bee decreased foraging success and survival in honey bees [73]. Clothianidin at 0.5 ng/bee resulted in adverse effects on bee foraging [35,74]. Chronic exposure of imidacloprid at 16 ng/g, or clothianidin at 17 ng/g reduced queen survival, worker movement, colony consumption, and colony weight in Bombus impatiens [75]. Only one of the 76 samples we collected might result in an exposure approaching 0.5 ng clothianidin/bee. However, the remaining samples resulted in a potential maximum dose exposure 1/10th that on a daily basis. These data suggest that the standing water in and around the commercial fields of maize sampled were unlikely contributors to sublethal effects on honey bees. However, we speculate that rain water puddles in fields of treated maize in the first weeks after planting may be a source of greater exposures.

Broadly, exposure to neonicotinoid insecticide residues would be greatly reduced if they were used more prescriptively than is currently the case. If most of the seed-applied neonicotinoids are targeted to the seed zone and remain associated with the sub-surface soil solution, based on our data, further limiting the amount of fugitive planter dust landing on the soil surface and limiting the number of exposed treated seeds remaining on the field surface are two practices that would reduce potential acute exposure to contaminated water available to foraging invertebrates within maize fields. These data are broadly informative to risk assessment models for other non-target organisms exposed to standing water in a maize agroecosystem. However, more field data are urgently needed to address the significant data gaps to inform tier three or greater [76] models for exposure risk assessment for non-target invertebrates to neonicotinoids in water; and we report these to assist ecotoxicologists in this urgent task.

Supporting Information

S1 Table. GPS coordinates of experimental fields, beeyards, drift snow and blank soil samples


S2 Table. Determination of 7 neonicotinoid residues (ng/mL) in water sampled within or in close proximity (≤ 100 m) of maize fields before and after planting in Ontario in 2013.


S3 Table. Summary of means for all water sample types collected, arranged by simple comparisons.


S4 Table. Determination of 7 neonicotinoids and 3 herbicide residues (ng/g; dry weight) using QuEChERS sample preparation and LC-ESI(+)-MS/MS analysis of two soil samples collected from a conservation forest of old growth Carolinian species.

Clear Creek Conservation Area, Chatham-Kent, ON 2013 (full data with subsamples).


S5 Table. Determination of 7 neonicotinoid insecticide and 3 herbicide residues (ng/g; dry weight) using QuEChERS sample preparation and LC-ESI(+)-MS/MS analysis of field soil in Ontario in 2013.


S6 Table. Determination of 7 neonicotinoid insecticide and 3 herbicide residues (ng/ml of melted snow) using QuEChERS sample preparation and LC-ESI(+)-MS/MS analysis in three snow drift samples collected in January 2014 from the edge of two harvested maize fields near Ridgetown, ON (full data with subsamples).



We would like to thank our grower and beekeeper co-operators for access to their assets and time. We could not have carried out this research without the dedication of the research technicians and summer staff including, Todd Phibbs, Jennifer Bruggeman, Darryl Galbraith, Morgan Kluka, Connor Gibney, Winfield Ly, Janet Lowther, Rob Seal, Lennard van Oord, Carissa Zandstra and Corina Bierling. We thank J. David Miller, Carleton University, for helpful suggestions in the preparation of this manuscript.

Author Contributions

Conceived and designed the experiments: AS VL YX TB JS. Performed the experiments: AS VL YX TB. Analyzed the data: AS YX VL JS. Contributed reagents/materials/analysis tools: AS VL TB JS. Wrote the paper: YX AS VL TB JS.


  1. 1. Kuhar TP, Stivers-Young LJ, Hoffmann MP, Taylor AG (2002) Control of corn flea beetle and Stewart’s wilt in sweet corn with imidacloprid and thiamethoxam seed treatments. Crop Protection 21: 25–31.
  2. 2. Elbert A, Haas M, Springer B, Thielert W, Nauen R (2008) Applied aspects of neonicotinoid uses in crop protection. Pest Management Science 64: 1099–1105. pmid:18561166
  3. 3. Hopwood J, Vaughan M, Shepherd M, Biddinger D, Mader E, et al. (2012) Are-neonicotinoids-killing-bees? A review of research into the effects of neonicotinoid insecticides on bees, with recommendations for action: The Xerces Society for Invertebrate Conservation.
  4. 4. Jeschke P, Nauen R, Schindler M, Elbert A (2011) Overview of the status and global strategy for neonicotinoids. Journal of Agricultural and Food Chemistry 59: 2897–2908 pmid:20565065
  5. 5. Steward G, Baute T (2013) Neonicotinoids and field crop production in Ontario. Available: Accessed 01 December 2014.
  6. 6. Biesmeijer JC, Roberts SPM, Reemer M, Ohlemu¨ller R, Edwards M, et al. (2006) Parallel declines in pollinators and insect-pollinated plants in Britain and the Netherlands. Science 313: 351–354. pmid:16857940
  7. 7. Goulson D, Lye GC, Darvill B (2008) Decline and conservation of bumble bees. Annual Review of Entomology 53: 191–208. pmid:17803456
  8. 8. Potts SG, Biesmeijer JC, Kremen C, Neumann P, Schweiger O, et al. (2010) Global pollinator declines: trends, impacts and drivers. Trends in Ecology & Evolution 25: 345–353. pmid:25619764
  9. 9. NRC (2007) Status of Pollinators in North America. Washington D.C.: National Academies Press.
  10. 10. vanEngelsdorp D, Underwood R, Caron D, Hayes J (2007) An estimate of managed colony losses in the winter of 2006–2007: A report commissioned by the Apiary Inspectors of America. American Bee Journal 147: 599–603.
  11. 11. vanEngelsdorp D, Hayes J, Underwood RM, Pettis J (2008) A survey of honey bee colony losses in the U.S., fall 2007 to spring 2008. PLoS ONE 3: 1–6 e4071.
  12. 12. CAAP (2007) CAPA Statement on Colony Collapse Disorder (CCD). Canadian Association of Professional Apiculturists.
  13. 13. Currie RW, Pernal SF, Guzmán-Novoa E (2010) Honey bee colony losses in Canada. Journal of Apicultural Research 49: 104–106.
  14. 14. Alaux C, Brunet J-L, Dussaubat C, Mondet F, Tchamitchan S, et al. (2009) Interactions between Nosema microspores and a neonicotinoid weaken honeybees (Apis mellifera). Environmental Microbiology 12: 774–782. pmid:20050872
  15. 15. Bacandritsos N, Granato A, Budge G, Papanastasiou I, Roinioti E, et al. (2010) Sudden deaths and colony population decline in Greek honey bee colonies. Journal of Invertebrate Pathology 105: 335–340. pmid:20804765
  16. 16. Guzman-Novoa E, Eccles L, Calvete Y, McGowan J, Kelly P, et al. (2010) Varroa destructor is the main culprit for death and reduced populations of overwintered honey bees in Ontario, Canada. Apidologie 4: 443–451.
  17. 17. Naug D (2009) Nutritional stress due to habitat loss may explain recent honey colony collapses. Biological Conservation 142: 2369–2372.
  18. 18. Mullin CA, Frazier M, Frazier JL, Ashcraft S, Simonds R, et al. (2010) High levels of miticides and agrochemicals in North American apiaries: implications for honey bee health. PLoS ONE 5: e9754. pmid:20333298
  19. 19. Pettis JS, vanEngelsdorp D, Johnson J, Dively G (2012) Pesticide exposure in honey bees results in increased levels of the gut pathogen Nosema. Naturwissenschaften 99: 153–158. pmid:22246149
  20. 20. Sharpe JR, Heyden LC (2009) Honey bee colony collapse disorder is possibly caused by a dietary pyrethrum deficiency. Bioscience Hypotheses 2: 439–440.
  21. 21. USDA (2012) Report on the national stakeholders conference on honey bee health. Alexandria, Virginia.
  22. 22. EPA/PMRA (2012) White paper in support of the proposed risk assessment process for bees. Available: Accessed 01 December 2014.
  23. 23. vanEngelsdorp D, Evans JD, Saegerman C, Mullin C, Haubruge E, et al. (2009) Colony collapse disorder: a descriptive study. PLoS ONE 3: e6481.
  24. 24. Vanengelsdorp D, Meixner MD (2010) A historical review of managed honey bee populations in Europe and the United States and the factors that may affect them. Journal of Invertebrate Pathology 103 Suppl 1: S80–95. pmid:19909973
  25. 25. Johansen CA, Mayer DF, Eves JD, Kious CW (1983) Pesticides and Bees. Environmental Entomology 12: 1513–1518.
  26. 26. Greatti M, Sabatini AG, Barbattini R, Rossi S, Stravisi A (2003) Risk of environmental contamination by the active ingredient imidacloprid used for corn seed dressing_Preliminary results. Bulletin of Insectology 56: 69–72.
  27. 27. Greatti M, Barbattini R, Stravisi A, Sabatini AG, Rossi S (2006) Presence of the a.i. imidacloprid on vegetation near corn fields sown with Gaucho dressed seeds. Bulletin of Insectology 59: 99–103.
  28. 28. Girolami V, Marzaro M, Vivan L, Mazzon L, Greatti M, et al. (2012) Fatal powdering of bees in flight with particulates of neonicotinoids seed coating and humidity implication. Journal of Applied Entomology 136: 17–26.
  29. 29. Pistorius J, Bischoff G, Heimbach U, Stähler M (2009) Bee poisoning incidents in Germany in spring 2008 caused by abrasion of active substance from treated seeds during sowing of maize. Hazards of pesticides to bees—10th International Symposium of the ICP-Bee Protection Group. pp. 118–126.
  30. 30. Pochi D, Biocca M, Fanigliulo R, Pulcini P, Conte E (2012) Potential exposure of bees, Apis mellifera L., to particulate matter and pesticides derived from seed dressing during maize sowing. Bulletin of Environmental Contamination and Toxicology 89: 354–361. pmid:22562269
  31. 31. Tapparo A, Marton D, Giorio C, Zanella A, Solda L, et al. (2012) Assessment of the environmental exposure of honeybees to particulate matter containing neonicotinoid insecticides coming from corn coated seeds. Environmental Science & Technology 46: 2592–1599. pmid:25626173
  32. 32. Krupke CH, Hunt GJ, Eitzer BD, Andino G, Given K (2012) Multiple routes of pesticide exposure for honey bees living near agricultural fields. PLoS ONE 7: e29268. pmid:22235278
  33. 33. Health Canada (2012) Evaluation of Canadian bee mortalities coinciding with corn planting in spring 2012 Category X.3; Submission Number 2012–1478.
  34. 34. Health Canada (2013) Evaluation of Canadian bee mortalities related with neonicotinoid pesticides. Interim Report as of September 26 2013.
  35. 35. EFSA (2013) Conclusion on the peer review of the pesticide risk assessment for bees for the active substance clothianidin. EFSA Journal 11: 3066.
  36. 36. EFSA (2013) Conclusion on the peer review of the pesticide risk assessment for bees for the active substance imidacloprid. EFSA Journal 11: 3068.
  37. 37. EFSA (2013) Conclusion on the peer review of the pesticide risk assessment for bees for the active substance thiamethoxam. EFSA Journal 11: 3067.
  38. 38. Nuyttens D, Devarrewaere W, Verboven P, Foqu´e D (2013) Pesticide-laden dust emission and drift from treated seeds during seed drilling: a review. Pest Management Science 69: 564–575. pmid:23456984
  39. 39. Bonmatin JM, Moineau I, Charvet R, Collin ME, Fleche C, et al. (2005) Behavior of imidacloprid in fields. Toxicity for honey bees. In: Lichtfourse E., Schwarzbauer J, Robert D, editors. Environmental Chemistry: Green Chemistry and Pollutants in Ecosystems. New York: Springer.
  40. 40. Laurent FM, Rathahao E (2003) Distribution of imidacloprid in sunflowers (Helianthus annuus L.) following seed treatment. Agricultural and Food Chemistry 51: 8005–8010. pmid:14690387
  41. 41. Stoner KA, Eitzer BD (2012) Movement of soil-applied imidacloprid and thiamethoxam into nectar and pollen of squash (Cucurbita pepo). PLoS ONE 7: e39114. pmid:22761727
  42. 42. Chauzat MP, Faucon JP, Martel AC, Lachaize J, Cougoule N, et al. (2006) A survey of pesticide residues in pollen loads collected by honey bees in France. Journal of Economic Entomology 99: 253–262. pmid:16686121
  43. 43. Girolami V, Mazzon L, Squartini A, Mori N, Marzaro M, et al. (2009) Translocation of neonicotinoid insecticides from coated seeds to seedling guttation drops: a novel way of intoxication for bees. Journal of Economic Entomology 102: 1808–1815. pmid:19886445
  44. 44. Hoffmann EJ, Castle SJ (2012) Imidacloprid in melon guttation fluid: a potential mode of exposure for pest and beneficial organisms. Journal of Economic Entomology 105: 67–71. pmid:22420257
  45. 45. Van Dijk TC, Van Staalduinen MA, Van der Sluijs JP (2013) Macro-invertebrate decline in surface water polluted with imidacloprid. PLoS ONE 8: e62374. pmid:23650513
  46. 46. Starner K, Goh KS (2012) Detections of the neonicotinoid insecticide imidacloprid in surface waters of three agricultural regions of California, USA, 2010–2011. Bulletin of Environmental Contamination and Toxicology 88: 316–321. pmid:22228315
  47. 47. Main AR, Headley JV, Peru KM, Michel NL, Cessna AJ, et al. (2014) Widespread use and frequent detection of neonicotinoid insecticides in wetlands of Canada’s prairie pothole region. PLoS ONE 9: e92821. pmid:24671127
  48. 48. Phillips PJ, Bode RW (2004) Pesticides in surface water runoff in south-eastern New York State, USA: seasonal and stormflow effects on concentrations. Pest Manag Sci 60: 531–543. pmid:15198325
  49. 49. Bonmatin JM, Giorio C, Girolami V, Goulson D, Kreutzweiser DP, et al. (2014) Environmental fate and exposure; neonicotinoids and fipronil. Environmental Science and Pollution Research Available: Accessed 01 December 2014. pmid:25096486
  50. 50. Schmaranzer S (2000) Thermoregulation of water collecting honey bees (Apis mellifera). Journal of Insect Physiology 46: 1187–1194. pmid:10818246
  51. 51. Nicolson SW (2009) Water homeostasis in bees, with the emphasis on sociality. Journal of Experimental Biology 212: 429–434. pmid:19151218
  52. 52. Kuhnholz S, Seeley TD (1997) The control of water collection in honey bee colonies. Behavioral Ecology and Sociobiology 41: 407–422.
  53. 53. Visscher PK, Crailsheim K, Sherman G (1996) How do honey bees (Apis mellifera) fuel their water foraging flights? Journal of Insect Physiology 42: 1089–1094.
  54. 54. Free JB, Spencer-Booth Y (1958) Observations on the temperature regulation and food consumption of honeybees (Apis Mellifera) Journal of Experimental Biology 35: 930–937.
  55. 55. Xing Z, Chow L, Rees H, Meng F, Li S, et al. (2013) Influences of sampling methodologies on pesticide-residue detection in stream water. Archives of Environmental Contamination and Toxicology 64: 208–218. pmid:23229193
  56. 56. Hladik ML, Kolpin DW, Kuivila KM (2014) Widespread occurrence of neonicotinoid insecticides in streams in a high corn and soybean producing region, USA. Environmental Pollution 193C: 189–196.
  57. 57. Environment Canada. 2014. Canadian climate normals: 1981–2010 climate normals & Averages. Available: Accessed 09 December 2014.
  58. 58. Anastassiades M, Lehotay SJ, tajnbaher D, Schenck FJ (2003) Fast and easy multiresidue method employing acetonitrile extraction/partitioning and “dispersive solid-phase extraction” for the determination of pesticide residues in produce. Journal of AOAC International 86: 412–431. pmid:12723926
  59. 59. Ramasubramanian T, Paramasivam M, Jayanthi R (2012) Rapid and sensitive analytical method for simultaneous determination of imidacloprid and thiamethoxam residues in soils of sugarcane ecosystem by reversed-phase hplc. Water, Air, & Soil Pollution 223: 6045–6050. pmid:25626179
  60. 60. Tanner G, Czerwenka C (2011) LC-MS/MS analysis of neonicotinoid insecticides in honey: methodology and residue findings in Austrian honeys. Journal of Agricultural and Food Chemistry 59: 12271–12277. pmid:22026460
  61. 61. Stokvis E, Rosing H, Beijnen JH (2005) Stable isotopically labeled internal standards in quantitative bioanalysis using liquid chromatography/mass spectrometry: necessity or not? Rapid Communications in Mass Spectrometry 19: 401–407. pmid:15645520
  62. 62. Currie LA (1999) Nomenclature in evaluation of analytical methods including detection and quantification capabilities: (IUPAC Recommendations 1995). Analytica Chimica Acta 391: 105–126.
  63. 63. Goulson D, Kleijn D (2013) An overview of the environmental risks posed by neonicotinoid insecticides. Journal of Applied Ecology 50: 977–987.
  64. 64. Health Canada (2013) CRUISER 350FS Seed Treatment. Accessed 01 December 2014
  65. 65. Health Canada (2013) PONCHO 600 FS Seed Treatment Insecticide. Available: Accessed 01 December 2014.
  66. 66. Health Canada (2013) Pollinator protection: reducing risk from treated seed. Available: Accessed 01 December 2014.
  67. 67. Beketov MA, Liess M (2008) Acute and delayed effects of the neonicotinoid insecticide thiacloprid on seven freshwater arthropods. Environmental Toxicology and Chemistry 27: 461–470. pmid:18348641
  68. 68. Jones A, Harrington P, Turnbull G (2014) Neonicotinoid concentrations in arable soils after seed treatment applications in preceding years. Pest Management Science. pmid:25534715
  69. 69. DeSutter TM, Clay SA, Clay DE (1998) Atrazine, alachlor, and total inorganic nitrogen concentrations of winter wind-eroded sediment samples. Journal of Environmental Science And Health Part B, Pesticides, Food Contaminants, and Agricultural Wastes 33: 683–691. pmid:9830132
  70. 70. Gibbons D, Morrissey C, Mineau P (2014) A review of the direct and indirect effects of neonicotinoids and fipronil on vertebrate wildlife. Environmental Science and Pollution Research: Available: Accessed 01 December 2014.
  71. 71. Chagnon M, Kreutzweiser D, Mitchell EAD, Morrissey CA, Noome DA, et al. (2014) Risks of large-scale use of systemic insecticides to ecosystem functioning and services. Environmental Science and Pollution Research: Available: Accessed 01 December 2014. pmid:25619818
  72. 72. Mommaerts V, Reynders S, Boulet J, Besard L, Sterk G, et al. (2010) Risk assessment for side-effects of neonicotinoids against bumblebees with and without impairing foraging behavior. Ecotoxicology 19: 207–215. pmid:19757031
  73. 73. Henry M, Beguin M, Requier F, Rollin O, Odoux JF, et al. (2012) A common pesticide decreases foraging success and survival in honey bees. Science 336: 348–350. pmid:22461498
  74. 74. Schneider CW, Tautz Jr, newald BG, Fuchs S (2012) RFID tracking of sublethal effects of two neonicotinoid insecticides on the foraging behavior of Apis mellifera PLoS ONE 7: e30023. pmid:22253863
  75. 75. Scholer J, Krischik V (2014) Chronic exposure of imidacloprid and clothianidin reduce queen survival, foraging, and nectar storing in colonies of bombus impatiens. PLoS ONE 9: e91573. pmid:24643057
  76. 76. EFSA (2013) EFSA Guidance Document on the risk assessment of plant protection products on bees (Apis mellifera, Bombus spp. and solitary bees). EFSA Journal 11: 3295.