1 Introduction

Many cultivated plants depend on bee pollination for fruit and seed production, as reviewed by Klein et al. (2007), and as such, bees are particularly important in light of the increasing demand for pollination services for agriculture food production (Chauzat et al. 2013; Breeze et al. 2014). Pollination deficits can lead to reduced yields, in turn leading to economic loss in agriculture systems; moreover, the estimated loss in ecosystem services provided by pollinators is valued at around €153 million annually (Gallai et al. 2009). The conspicuous and ever-growing use of agriculture pesticides is a recognized threat to bee populations and the ecological services they provide, particularly that of pollination (Sanchez-Bayo and Goka 2014; Barbosa et al. 2015b; Guedes et al. 2016). Thus, risk analyses of pesticides are needed in order to assess such potential threats, encompassing not only lethal but also sublethal exposure via contact and ingestion, in both honeybee and native bee pollinator populations (Van der Sluijs et al. 2013; Fairbrother et al. 2014; Barbosa et al. 2015b; Lima et al. 2016).

Many of the lethal and sublethal effects of synthetic pesticides on honeybees are broadly recognized and have been extensively reported in the scientific literature (e.g., Arena and Sgolastra 2014; Fairbrother et al. 2014; Staveley et al. 2014). However, such studies have largely focused on honeybees and neonicotinoid insecticides (Barbosa et al. 2015b), and a handful of other synthetic compounds (Suri and Singh 2011; Valk and Koomen 2012; Godfray et al. 2014; Roubik 2014). One of the consequences of such emphasis is a growing interest in the use of alternative pesticidal compounds, primarily those of natural origin, which are commonly referred to as biopesticides (Isman 2006; Gerwick and Sparks 2014; Villaverde et al. 2014; Guedes et al. 2016). Nonetheless, given that the source of origin is not a determinant of biological activity, the common perception that biopesticides are safer to pollinators is misguided (Coats 1994; Bahlai et al. 2010; Barbosa et al. 2015b; Guedes et al. 2016). This prevailing notion, however, has led to a knowledge gap regarding the potential impacts of biopesticides on pollinators, although recent studies indicate that the impacts of biopesticide compounds on some bee pollinators may be significant (Barbosa et al. 2015a; Barbosa et al. 2015b; Barbosa et al. 2015c; Tomé et al. 2015a; Tomé et al. 2015b).

The botanical biopesticide azadirachtin, obtained from the Indian neem tree (Azadirachta indica A. Juss. [Meliaceae]), is the most widely used natural pesticide today. The initial optimism regarding its safety on non-target species has, however, subsequently been replaced by a more cautious posture (e.g., Barbosa et al. 2015a; Barbosa et al. 2015b; Barbosa et al. 2015c; Cordeiro et al. 2010; Lima et al. 2015). The use of azadirachtin and derived products is still increasing (Isman 2006; Isman and Grieneisen 2014), likely due to its appeal as an efficacious biopesticide with a rapid environmental breakdown (Boeke et al. 2004; Isman and Grieneisen 2014). As such, the lack of research on the potential impacts of azadirachtin on bee pollinator species remains a concern worthy of greater attention.

Another serious bias of studies of insecticide-pollinator interactions is the overwhelming focus on honeybees, often at the expense of native bee fauna (Valk and Koomen 2012; Barbosa et al. 2015b; Lima et al. 2016). The stingless bee fauna of megadiverse tropical countries illustrates the importance of this group of native pollinators, not only for cultivated crops but also for native plant species (Kremen et al. 2002; Del Sarto et al. 2005; Barbosa et al. 2015b). The scarcity of information available regarding the decline of this group of pollinators, and the threat imposed by pesticides, biopesticides included, to these species, justifies the concern, as does research indicating that stingless bees are generally more vulnerable to these compounds than are honeybees (Tomé et al. 2012; Arena and Sgolastra 2014; Del Sarto et al. 2014; Barbosa et al. 2015a, 2015c; Tomé et al. 2015a; Tomé et al. 2015b). Our goal here was to redress this knowledge gap somewhat by assessing the potential impacts of azadirachtin on two species of stingless bee pollinator species, Melipona quadrifasciata Lepeletier and Partamona helleri Friese.

In this experiment, adult foraging workers of the two stingless bee species were exposed to field rates of the biopesticide azadirachtin via contact and oral exposure, and their lethal and sublethal effects were recorded. The relative species-dependent toxicity usually associated with azadirachtin makes predictions of its toxicity difficult, but, based on the few studies available with pollinators, this insecticide is unlikely to cause high acute mortality in stingless bees, although significant sublethal effects are likely to occur (Barbosa et al. 2015a, 2015c; Lima et al. 2016).

2 Material and methods

2.1 Bees and insecticide

Bee specimens of both species were collected from five colonies each of M. quadrifasciata and P. helleri in Viçosa county, in the state of Minas Gerais, Brazil (20° 45′ S and 42° 52′ W), and established in the experimental apiary of the Federal University of Viçosa. The adult foraging bees used in the experiment were collected at the colony entrance of each hive using glass jars and were subsequently taken to the laboratory. The insects were maintained without food in wooden cages (35 cm × 35 cm × 35 cm) covered with organza and kept under environmentally controlled conditions (25 ± 2 °C, 70 ± 10 % relative humidity, 24-h scotophase) for 1 h, following which they were subjected to the bioassays.

A commercial azadirachtin-based insecticide formulation was used in the study (Azamax, 12 g a.i./L, emulsifiable concentrate; DVA Agro Brasil, Campinas, SP, Brazil) and diluted either in deionized and distilled water (for contact exposure bioassays) or in 50 % (w/w) aqueous sucrose solution (for oral exposure bioassays). The azadirachtin concentrations used in the bioassay exposures consisted of the maximum field rate (30 mg a.i./L) and twice the maximum field rate (60 mg a.i./L); controls were exposed only to the solvent (i.e., either water or 50 % aqueous sucrose solution). The maximum field rate used was based on the recommended concentration for control of the whitefly Bemisia tabaci (Gennadius) (Hemiptera: Sternorrhyncha: Aleyrodidae) in open tomato fields in Brazil (Ministério da Agricultura, Pecuária e Abastecimento 2015).

2.2 Time-mortality (survival) bioassays

Contact and oral exposure time-mortality bioassays were performed with adult foraging workers of both stingless bee species, with identical methods adopted for both species. We followed the procedures described by Tomé et al. (2015b), in which the contact bioassays were performed using 250-mL transparent containers with inner walls impregnated with 500 μL insecticide solution (or water for controls) using an artist’s air brush (Sagyma SW440A, Yamar Brasil, São Paulo, SP, Brazil) coupled with an air pump (Prismatex 131A Tipo 2 VC, Itu, SP, Brazil) at a pressure of 6.9 × 104 Pa. The sprayed containers were dried for 2 h in a dark exhausting chamber kept at 25 ± 3 °C. Then, 10 adult non-starved worker bees were released into each container, which were covered by organza in the upper part to prevent the insects from escaping. Each container corresponded to an experimental unit, and five containers, each with insects from a single colony (i.e., five colonies, or replicates) were used for each species and insecticide treatment (and control). Uncontaminated sucrose solution was provided ad libitum to the bees via a feeder extending through a hole in the containers, regardless of the treatment; the feeder allowed only a single insect to feed at a time and the feeding was brief with the other nine insects maintaining contact with the contaminated surface of the container. After 3 h of exposure, the treated insects were transferred to uncontaminated containers and fed uncontaminated sucrose solution. Survival was assessed at 1-h intervals for 24 h, with mortality defined as those insects unable to walk the length of their body.

The same experimental units of the contact bioassay were also used for the oral exposure bioassays, including the same number of insects and replicates. However, insecticide exposure in this case was achieved by providing 500 μL of azadirachtin-contaminated sucrose solution (except for untreated controls) in drilled Eppendorf® tubes used as feeders and inserted through a hole in each of the 250-mL transparent containers, each one with 10 bees of each species. The bees were kept in uncontaminated containers throughout this experiment. Food was withheld from the adult foragers for 1 h, after which they were allowed to feed for 3 h either in azadirachtin-contaminated or uncontaminated (i.e., control) diet; following this, the bees were provided with uncontaminated sucrose solution. The insecticide dose ingested was obtained by weighing the feeders before and after the experiment and dividing by the number of bees in the container. Mortality was recorded at 6, 9, 12, 24, 48, and 72 h after the beginning of the exposure. The worker was considered as dead if unable to walk the length of their body.

2.3 Feeding bioassays

Food consumption and potential antifeedant effects caused by azadirachtin exposure were evaluated through two bioassays. Feeding avoidance (i.e., antifeeding effect) was assessed in individual bees, while food consumption was assessed in groups of 10 worker bees of the same colony to allow for the group effect on these social organisms; otherwise, consumption is likely compromised. Preliminary investigation with both species indicated an average consumption of 10 ± 1 μL sucrose per bee within a 1-min period. Therefore, for the feeding avoidance bioassay, each individual worker bee was provided with 4 μL of sucrose solution (azadirachtin-contaminated, excepted with the control treatment) as a drop at the bottom of the horizontal glass vials (15 cm length × 2 cm diameter) where the individual bees were maintained for 5 min ensuring the ingestion of the whole solution after 1 h of starvation. The bioassay was carried out with 10 foraging workers from each of the same five colonies previously used, which were tested in each azadirachtin treatment (0, 30, and 60 mg a.i./L). The adult bees were attracted by a light source at the outside of the bottom of the feeder, following the procedure outlined by Barbosa et al. (2015a). After this period of 5-min exposure, the bees were transferred to identical containers maintained at the same conditions and with provision of 4 μL of uncontaminated sucrose diet and allowed to feed for an additional 5-min period. All of the bees ingested the contaminated diet (except the controls, which fed on uncontaminated diet). The number of bees feeding on the uncontaminated diet after the initial 5-min exposure to the azadirachtin-contaminated diet (except for the control) was recorded to assess whether azadirachtin ingestion impairs subsequent feeding.

The intake of diet after azadirachtin exposure was assessed in a complementary food consumption bioassay where adult workers were maintained in 250 mL containers, as in the time-mortality bioassays for oral exposure. Each container had a group of 10 bees of a given colony (for a total of five colonies, or replicates, per treatment) provisioned with diet (i.e., sucrose solution with either 0, 30, or 60 mg azadirachtin/L) for 3 h. These workers were subsequently transferred to 250-mL containers provisioned with uncontaminated diet, as previously described. The feeders were replenished with uncontaminated sucrose diet in each treatment, and the diet consumption was recorded at 6, 9, 12, 24, 48, and 72 h by weighing the food provided before and after these periods of ingestion. Thus, the frequency of bees exhibiting food avoidance following azadirachtin exposure was recorded in the first consumption bioassay and food ingestion was recorded in the second, also after azadirachtin exposure.

2.4 Walking bioassays

Twelve adult worker bees (3-day old) were collected from individualized brood combs taken from the five different colonies of each species upon progeny pupation (Tomé et al. 2012). Therefore, in this experiment, we used 120 bees (12 bees × 5 colonies × 2 treatments), which were individually subjected to walking bioassays on azadirachtin half-treated arenas, in accordance with previously described methods (Guedes et al. 2009; Cordeiro et al. 2010). Briefly, filter paper discs (9 cm in diameter with porosity of 3 μm, 0.5 % ash content, and 80 g/m2 density; Nalgon Equip. Científicos, Itupeva, SP, Brazil) were treated with 1 mL of azadirachtin (or water) solution at the same concentration of the previous bioassays. Each arena was composed of a water-treated filter paper fixed to the bottom of a Petri dish, with half of the azadirachtin-treated disc fixed over the control disc using water-based white (synthetic) glue resin, such that half of the arena was treated with azadirachtin and the other half left untreated; both halves were left untreated in the control treatment. The inner walls of the Petri dish arenas were coated with Teflon TPFE® (DuPont, Wilmington, DE, USA) to prevent the bees from escaping. A single 3-day-old adult worker was released into the center of each arena, and the arena then placed under a video tracking system (ViewPoint LifeSciences, Montreal, Quebec, Canada). The walking bees were recorded for 10 min, after which the videos were digitally transferred to a computer. This system allowed calculation of the time spent in each half of the arena (azadirachtin-treated and untreated) and thus indication of potential repellence (i.e., number of bees spending less than 1 s on the azadirachtin-treated half of the arena) and irritability (i.e., number of bees remained for longer on the untreated half of the arena) triggered by azadirachtin.

2.5 Flight takeoff bioassays

Flight takeoff bioassays were performed with adult foraging workers following exposure to azadirachtin either by contact or ingestion, as previously detailed in the time-mortality (survival) bioassays. After a 3-h period of exposure to azadirachtin (0, 30, and 60 mg of azadirachtin/L) and a 24-h period under uncontaminated conditions, the insects were individually subjected to the flight takeoff bioassays, following the procedure described by Tomé et al. (2015b). For this bioassay, a three-staked wooden cage tower was used (35 cm × 35 cm × 35 cm, each forming a 105-cm tall tower) that allowed for unrestricted movement and flight. A fluorescent lamp was placed 5 cm above the tower in a dark room to attract the flying worker bees. An individual foraging worker was then released from a Petri dish at the center bottom of the tower after a 1-min acclimation and cover removal allowing the insect to take off for flight. Vertical flight takeoff and activity was observed for 2 min and recorded as (a) no flight, (b) flight up to a height of 35 cm, (c) flight between heights of 35 and 70 cm, (d) flight between heights of 71 and 105 cm, and (e) flight reaching the light source at a height of 110 cm. Fifty bees from different colonies (i.e., 10 from each of the five colonies) were used for each insecticidal treatment and mode of exposure. The flight activity was recorded for each individual bee and colony. The worker bees treated with water only (control) were from the same colonies as the azadirachtin-exposed bees and they were all maintained under the same conditions.

2.6 Respirometry bioassays

Bees exposed to azadirachtin both by contact and oral ingestion were also subjected to respirometry bioassays, as respiratory rhythms can indicate behavioral and ontogeny alterations in stingless bees (Teixeira et al. 2011). Thus, following azadirachtin exposure as previously described for the survival bioassays, five individual insects from each colony (i.e., independent biological replicates) and subjected to each azadirachtin treatment in both types of exposure (i.e., contact and oral exposure) were individually enclosed in 25-mL glass containers connected to a completely closed system (TR3C respirometer equipped with a CO2 analyzer; Sable Systems International, Las Vegas, NV, USA). The CO2 production (μL CO2/h/bee) was determined after a 3-h period by injecting CO2-free air into the chamber for 2 min at a flow rate of 600 mL/min. The air current was directed to an infrared reader connected to the system, allowing for the determination of the CO2 produced per bee.

2.7 Statistical analyses

Kaplan-Meier estimators were used to calculate survival curves and estimates of median survival times (LT50’s), when appropriate (PROC LIFETEST; SAS Institute 2008). Normality and homoscedasticity assumptions were tested for food consumption, walking, flight takeoff, and respirometry results (PROC UNIVARIATE; SAS Institute 2008). A paired t test was used to analyze walking data, whereas a Wilcoxon rank sum test was used to analyze food avoidance results (PROC FREQ; SAS Institute 2008). Food consumption results were tested via repeated measures analyses of variance, with time as a pseudoreplicate (PROC ANOVA with PROFILE statement; SAS Institute 2008). Finally, flight takeoff data were subjected to a (non-parametric) Kruskal-Wallis test (P < 0.05) (PROC NPAR1WAY; SAS Institute 2008).

3 Results

3.1 Time-mortality (survival) response

Azadirachtin did not cause any bee mortality up to 24 h of contact exposure for M. quadrifasciata (χ 2 = 0.098, df = 2, P = 0.952) and P. helleri (χ 2 = 0.200, df = 2, P = 0.905). Similarly, no mortality was observed for either M. quadrifasciata (χ 2 = 0.202, df = 2, P = 0.904) or P. helleri (χ 2 = 1.333, df = 2, P = 0.513) in any treatment (azadirachtin and control) up to 72 h following oral exposure. Therefore, no lethal effect of azadirachtin was detected after neither via of exposure for the species studied, and as such, median lethal times could not be estimated for any treatment.

3.2 Food avoidance and consumption

Azadirachtin did not elicit food avoidance in the stingless bee species M. quadrifasciata (χ 2 = 2.45, df = 2, P = 0.30, Figure 1a). In contrast, azadirachtin did elicit food avoidance (of uncontaminated diet) among workers of P. helleri, particularly at the highest azadirachtin concentration, which corresponded to twice the registered label rate (χ 2 = 18.91, df = 2, P < 0.001, Figure 1b). Food consumption, however, was more distinctly affected by the presence of azadirachtin. Such differences, although significant for M. quadrifasciata, particularly after shifting to the uncontaminated diet (F 1,2 = 5.98, P = 0.01), were soon recovered (Figure 2a), with little effect on cumulative food consumption observed after 6 h of feeding on the uncontaminated diet (Figure 2b). P. helleri was more drastically affected by early ingestion of the azadirachtin-contaminated diet (F 1,2 = 7.88, P = 0.006), which impaired subsequent food consumption through time and retaining lower levels of food intake through to the end of the observation period, at 72 h (Figure 2c, d).

Figure 1.
figure 1

Feeding avoidance (primary antifeedancy) of an uncontaminated diet by foraging workers of two stingless bee species, M. quadrifasciata (a) and P. helleri (b), orally exposed to azadirachtin for 5 min. Histogram bars with the same letters are not significantly different by the Wilcoxon rank sum test (P < 0.05).

Figure 2.
figure 2

Consumption (mean ± SE) of uncontaminated feed by foraging workers of two stingless bee species, M. quadrifasciata (a, b) and P. helleri (c, d), orally exposed to azadirachtin. Asterisks indicate significant differences between treatments by Fisher’s F test (P < 0.05).

3.3 Walking response

Representative walking tracks of adult worker bees of both species when released on half-treated arenas are exhibited in Figure 3. Although azadirachtin did not elicit repellence at the field rate in either bee species (M. quadrifasciata: t 4 = 0.91, P = 0.41; P. helleri: t 4 = 1.27, P = 0.27), this biopesticide elicited significant irritability at twice the field rate for M. quadrifasciata (t 4 = 3.15, P = 0.03; Figure 4a), but not for P. helleri (t 4 = 1.75, P = 0.15; Figure 4b), in response to contact exposure.

Figure 3.
figure 3

Representative tracks showing the walking activity of workers of two stingless bee species, M. quadrifasciata and P. helleri, over a 10-min period on paper-filter arenas (9 cm diameter) half impregnated with dried azadirachtin residues (upper half of each arena). Red tracks indicate high walking velocity; green tracks indicate low (initial) velocity.

Figure 4.
figure 4

Insecticide irritability of workers of two stingless bee species, M. quadrifasciata (a) and P. helleri (b), exposed for a 10-min period on paper-filter arenas (9 cm diameter) half impregnated with dried azadirachtin residues. Asterisks on histogram bars indicate significant differences between the treated and untreated halves of the arena (t test; P < 0.05).

3.4 Flight takeoff response

Flight takeoff performance was assessed for azadirachtin-exposed and unexposed adult foraging workers, but no significant effect was detected for either ingestion or contact exposure regardless of the species (H < 1.82, df = 2, P > 0.40). For ingestion exposure, the average timed response for M. quadrifasciata was 13.59 ± 3.74 s and for P. helleri 11.80 ± 4 s; for contact exposure, the average timed response for M. quadrifasciata was 10.34 ± 3.4 s and for P. helleri 12.12 ± 4.5 s.

3.5 Respiration rate

Azadirachtin did not affect the respiration rate of bees of either species exposed by contact or exposure (P > 0.05). Contact-exposed worker bees of M. quadrifasciata exhibited an average respiration rate of 0.28 ± 0.03 μL CO2/h/bee (F 1,2 = 0.43, P = 0.65), whereas worker bees of P. helleri exhibited an average respiration rate of 0.10 ± 0.02 μL CO2/h/bee (F 1,2 = 0.04, P = 0.95). Orally exposed worker bees of M. quadrifasciata exhibited an average respiration rate of 0.32 ± 0.04 μL CO2/h/bee (F 1,2 = 1.07, P = 0.37), whereas worker bees of P. helleri exhibited an average respiration rate of 0.10 ± 0.02 μL CO2/h/bee (F 1,2 = 0.10, P = 0.90).

4 Discussion

In this study, we assessed the potential impacts of the biopesticide azadirachtin on adult workers of two stingless bee species, M. quadrifasciata and P. helleri, through both contact and oral exposure routes. Based on the results of the few previous studies available, we did not expect azadirachtin to induce high acute mortality, but considered sublethal effects to be more likely, although azadirachtin toxicity appears to be species dependent even among pollinators (Barbosa et al. 2015a, Barbosa et al. 2015c). Indeed, our results were congruent with such expectations, as we observed negligible acute mortality following contact and oral exposure to azadirachtin. However, sublethal effects on walking activity and food consumption were detected varying with the stingless bee species.

The lack of azadirachtin repellence to both pollinator species indicates that they are unlikely to avoid field exposure to azadirachtin-contaminated flowers and will collect contaminated resources. The irritability to azadirachtin-contaminated surfaces exhibited by workers of M. quadrifasciata will likely reduce the collection of large amounts of contaminated resources. Nonetheless, such irritability occurred only at high azadirachtin concentrations, a scenario unlikely to take place under field conditions. In contrast, P. helleri did not exhibit irritability to azadirachtin-contaminated surfaces. This finding reinforces the risk of exposure to azadirachtin for both stingless bees under field conditions, unlike the reports with other insect and mite species that exhibit azadirachtin irritability and even repellence (Cordeiro et al. 2010; Lima et al. 2013).

The differences between the feeding behavior of both stingless bees after azadirachtin ingestion also deserve attention. Because workers of P. helleri exhibited concentration-dependent azadirachtin feeding avoidance and also reduced food consumption, colonies of this species are more likely to be harmed by azadirachtin than M. quadrifasciata. Azadirachtin is characterized as a growth regulator and sterilant insecticide but has also been shown to induce antifeeding behavior in insects (Mordue (Luntz) et al. 1998; Mordue (Luntz) and Nisbet 2000). The former two effects are irrelevant for adult worker bees, given that they are already fully developed and sterile, but larval exposure to azadirachtin may result in a different outcome (Tomé et al. 2015a), and insufficient feeding may impair worker foraging. However, the antifeeding behavior observed in P. helleri, but not M. quadrifasciata, suggests that the former will have a smaller risk of contamination than the latter.

In addition to azadirachtin, several other compounds in the plant biosynthetic pathway leading to its production have antifeedant properties (Aerts and Mordue (Luntz) 1997). The early feeding avoidance (i.e., primary antifeedancy) seems to be mediated by (gustatory) contact chemoreception, but internal feedback mechanisms may also take place that lead to toxic consequences to the insect (i.e., secondary antifeedancy) (Trumm and Dorn 2000; Mordue (Luntz) et al. 2010). Such effects are known to vary with insect species (Mordue (Luntz) et al. 2010), as observed here for stingless bees. The primary antifeeding response to azadirachtin is a result of the stimulation of deterrent (gustatory) chemoreceptors by azadirachtin, which also is believed to have inhibitory effects on the firing of sucrose-sensitive cells of the gustatory chemoreceptors (Simmonds and Blaney 1984, 1996).

Several species have been shown to be extremely sensitive to the primary antifeedant properties of azadirachtin, thus, starving to death rather than ingesting the biopesticide (Mordue (Luntz) et al. 2010). Such an effect on P. helleri was significant only at azadirachtin concentrations twice that of the label rate. However, this feeding avoidance behavior remained even when the bees were provided with an uncontaminated diet, and their food consumption was also compromised, what may also compromise future foraging. Secondary antifeedancy effects were not assessed in our experiments, but likely occur and may explain the subsequent feeding avoidance and reduced diet consumption behaviors exhibited by P. helleri following exposure to azadirachtin.

Biopesticides, of which azadirachtin is one of the most prominent examples under commercial worldwide use (Isman 2006; Isman and Grieneisen 2014), are generally regarded as safer to non-target arthropod species, despite the lack of a proven relationship between origin (either natural or synthetic) and toxicity (Coats 1994; Barbosa et al. 2015b; Guedes et al. 2016). Such a notion, although misguided in many cases, does appear to be valid for azadirachtin and stingless bees, with only one of the two tested species exhibiting mild susceptibility to the antifeedant effects of the compound. Yet, these effects may be important, however, since they appear to compromise subsequent foraging and reduce feeding by foraging workers. Moreover, we focused solely on the impacts of azadirachtin exposure on adult bees, whereas larval exposure to azadirachtin may be of even greater importance given that the developmental stages are more vulnerable to the growth regulator properties of this biopesticide.

Another point of concern is that, as reported in this manuscript, the impacts of azadirachtin exposure can vary quite considerably even between the two species of stingless bees (Meliponini). Therefore, although only one of the tested species (P. helleri) was significantly affected at a sublethal level by azadirachtin, other species of stingless bees may prove to be more susceptible. This topic deserves future attention, especially in light of the fact that honeybees are questionable surrogates for stingless bees in pesticide impact assessments (Arena and Sgolastra 2014; Barbosa et al. 2015b).