PAGES: 458-465 DOI: 10.1590/S0074-02762012000400003 Full paper
Evolution of insecticide resistance in non-target black flies (Diptera: Simuliidae) from Argentina

Cristina Mónica MontagnaI, +; Lidia Ester GaunaI; Ana Pechen de D'AngeloII; Olga Liliana AnguianoII

IFacultad de Ciencias del Ambiente y de la Salud, Instituto Multidisciplinario de Investigación y Desarrollo de la Patagonia Norte, Universidad Nacional del Comahue, Buenos Aires 1400, (8300) Neuquén, Argentina
IIFacultad de Ingeniería, Instituto Multidisciplinario de Investigación y Desarrollo de la Patagonia Norte, Universidad Nacional del Comahue, Buenos Aires 1400, (8300) Neuquén, Argentina


Black flies, a non-target species of the insecticides used in fruit production, represent a severe medical and veterinary problem. Large increases in the level of resistance to the pyrethroids fenvalerate (more than 355-fold) and deltamethrin (162-fold) and a small increase in resistance to the organophosphate azinphos methyl (2-fold) were observed between 1996-2008 in black fly larvae under insecticide pressure. Eventually, no change or a slight variation in insecticide resistance was followed by a subsequent increase in resistance. The evolution of pesticide resistance in a field population is a complex and stepwise process that is influenced by several factors, the most significant of which is the insecticide selection pressure, such as the dose and frequency of application. The variation in insecticide susceptibility within a black fly population in the productive area may be related to changes in fruit-pest control. The frequency of individuals with esterase activities higher than the maximum value determined in the susceptible population increased consistently over the sampling period. However, the insecticide resistance was not attributed to glutathione S-transferase activity. In conclusion, esterase activity in black flies from the productive area is one mechanism underlying the high levels of resistance to pyrethroids, which have been recently used infrequently. These enzymes may be reselected by currently used pesticides and enhance the resistance to these insecticides. 

Black flies (Diptera: Simuliidae) are found worldwide, in America from north (Canada) to south (Argentina) as well as in Europe, Africa, Asia, Oceania and Antarctica continents (Crosskey & Howard 2004, Currie & Adler 2008). Black flies breed in fast-flowing streams and they are usually pests of medical and veterinary importance, with approximately 2,000 nominal species (Currie & Adler 2008). Black flies are nuisance insects and some species are fierce biters that cause allergic reactions and dermatitis in sensitised individuals (De Villiers 1987, Williams 1991, Youssefi et al. 2008). Some black flies are also vectors of human diseases in many countries (Hougard et al. 1992, Shelley 2002). They also attack livestock, causing economic losses due to reductions in milk and beef production (Schmidtmann et al. 2001).

Black fly control programmes have primarily been implemented to arrest the transmission of Onchocerca volvulus in Africa and Central and South America through the use of larvicides or adulticides (McMahon 1967). Some of the larvicides have included the organochlorines DDT, HCH and dieldrin, the organophosphates temephos and chlorphoxim, the carbamate carbosulfan and the pyrethroid permethrin (McMahon 1967, Yamagata et al. 1987, Hougard et al. 1992, Paugy et al. 1999). In addition, biological control with Bacillus thuringiensis var. israelensis has been successfully implemented in Africa (Rivers-Moore et al. 2008), Brazil (Regis et al. 2000) and other countries such as Lithuania, where outbreaks of bloodsucking black flies affect daily human activities (Bartninkait? et al. 2006). Because of the success of the Onchocerciasis Control Program in West Africa and Central and South America, which utilises both biopesticides against the vector (B. thuringiensis) and the parasite (ivermectin) (Etya'ale 2001), there have only been a few reported cases of insecticide resistance in black fly populations that are vectors of O. volvulus (Ruas Neto 1984, Hougard et al. 1992).

Three species of black flies have been identified in the Río Negro and Neuquén Valley (Coscarón 1997): Simulium bonaerense (Coscarón and Wygodzinsky), Simulium wolffhuegeli (Enderlein) and Simulium nigristrigatum (Wygodzinsky and Coscarón). All three species are nuisance and biting pests of humans and livestock. These non-target species are found from spring to autumn and their development overlaps with the seasonal pesticide spraying used to control Cydia pomonella (L.) and other fruit tree pests in the Río Negro and Neuquén Valley. C. pomonella has three generations per year and pest control programmes in the previous century have included several applications of broad-spectrum insecticides, principally pyrethroids. During the 1993-1994 growing season, many farmers began to report control failures with pyrethroids, especially esfenvalerate. Subsequently, azinphos methyl was primarily recommended for codling moth management along with other unconventional insecticides. In recent years, although conventional pesticides such as azinphos methyl, carbaryl and pyrethroids are still applied, neonicotinoids (acetamiprid, thiacloprid), rynaxypyr, insect growth regulators (novaluron) and microbial insecticides (spinosad) are the primary choices for many farmers.

Because black fly populations breed successfully in the channel network that was implemented to manage water for fruit production, they are subjected to pesticide residues via spray drift and run-off. Pesticide spraying also reaches adult black flies at their resting sites.

High levels of resistance to DDT and pyrethroids were found in non-target black flies from the Río Negro and Neuquén Valley by the end of the previous century (Montagna et al. 1999, 2003). Other authors have also attributed insecticide resistance in black flies (Andrade & Branco 1990, Osei-Atweneboana et al. 2001) and mosquito populations (Diabate et al. 2002) to agricultural pesticide use.

The aim of this study was to evaluate the development and mechanisms of fenvalerate, deltamethrin and azinphos methyl resistance in non-target black fly populations from a fruit production area in Northern Patagonia (Argentina) over a period of 13 years.



Chemicals - The insecticides fenvalerate [93.9-97% active ingredient (AI)], deltamethrin (96.5-99.8% AI) and azinphos methyl (96.5-99% AI) were purchased from AccuStandard Inc, New Haven, CT, USA and Chemical Service Inc, West Chester, PA, USA. Reduced glutathione, 1-chloro-2,4-dinitrobenzene (CDNB), ?-naphthyl acetate, ?-naphthol (?-N), Fast Garnet GBC salt, Triton X-100, bovine serum albumin (BSA) and 1,5-bis(4-allyldimethylammonium phenyl)pentan-3-one dibromide (BW284C5) were purchased from Sigma Chemical Co, St. Louis, MO, USA.

Study area - The insecticide-exposed population was collected from an important irrigation channel at Fernández Oro (FO) (38º16'S 67º45'W). A population collected upstream at Piedra del Águila (PA) (lat. 42º2'S 70º5'W), which had no history of pesticide application and thus had a more susceptible population, was used as a field-reference population (Montagna et al. 1999, 2003). Larvae of Simulium spp were collected from the studied areas (from October-early March) and were attached to aquatic weeds, such as Potamogeton pectinatus and Chara vulgaris L., or submerged branches of Salix babylonica L. and transported to the laboratory inside a cool box. The larval sample size was always variable (from approximately 100-600 larvae) and depended on the weather conditions and the available vegetation (vegetation from the channel is periodically removed mechanically).

Toxicity assays - Bioassays were performed immediately after the selection of fifth instars with white histoblasts. The bioassays on field populations of the Simulium larvae were performed according to a previously described procedure (Montagna et al. 1999, 2003). Groups of 20 larvae were exposed to > four concentrations (except in those cases in which the larvae exhibited a very homogeneous response) of technical-grade insecticide dissolved in 0.1 mL acetone in a final volume of 200 mL filtered dechlorinated water. Each test was replicated at least three times on different days. The larvae were maintained at 15 ± 1ºC for 24 h with a photoperiod of 16:8 (L:D) h. The mortalities of both the treated and control larvae were determined after this treatment.

Enzyme activity - Fifth instar larvae with white histoblasts were selected immediately after the field collection and individually frozen at -20ºC for a few days until the enzyme assays were performed. The non-specific esterase activity was determined individually (Dary et al. 1990). The larvae were homogenised with a Teflon homogenisation rod in 100 µL 0.1 M sodium phosphate buffer (pH 6.5) containing 0.5% Triton X-100. Each sample was centrifuged at 700 g for 20 s and the supernatant was used as the enzyme source. A 20-µL aliquot of the supernatant was diluted into the homogenisation buffer to obtain values within the linear range of the assay. Aliquots of 50 µL were loaded in a 96-well ELISA plate incubated on ice. The reaction was initiated in each well by the addition of 100 µL developing solution. The developing solution contained distilled water, 0.1 M sodium phosphate buffer (pH 6.5), 0.5% Triton X-100, final concentration 2 mM ?-NA in ethanol and 0.002 mM BW284C5 in ethanol. The microplate was then removed from the ice and its contents were mixed; esterase hydrolysis was allowed to proceed for 15 min. Next, 100 µL 2.5 mM Fast Garnet GBC salt was added and the absorbance at 550 nm was recorded after 10 min with a microplate reader (Molecular Devices, Sunnyvale, CA, USA). The absorbance values were transformed to µmoles of ?-N according to an ?-N standard curve. Each enzyme preparation was replicated twice.

Glutathione S-transferase (GST) activity towards CDNB (0.5 mM in acetonitrile) was determined with batches of 25 larvae homogenised in 66 mM phosphate buffer containing 25 mM sucrose (pH 7.0) according to the method described by Habig et al. (1974). Each sample was centrifuged at 10,000 g for 20 min at 4ºC and the supernatants were used without further purification. The reaction mixture consisted of 2.77 mL 0.1 M phosphate buffer (pH 6.5), 50 µL enzyme source, 30 µL CDNB and 150 µL 2.5 mM reduced glutathione in a final volume of 3 mL. The absorbance was recorded continuously at 340 nm for 2 min with a ultra-violet/visible spectrophotometer (Shimadzu, Kyoto, Japan). The rate measurements were corrected for the non-enzymatic reaction. The absorbance values were transformed to µmoles of CDNB conjugates with an extinction coefficient of 9.6 mM-1 cm-1. At least five different enzyme preparations for each population were assayed.

The protein preparations were assayed for esterase or GST activity according to the method of Lowry et al. (1951) individually or as a batch of supernatants from 25 larvae, respectively. The absorbance at 750 nm was measured and transformed into a protein concentration according to a BSA standard curve.

Statistical analysis - Lethal concentration fifty (LC50) values were calculated from a probit analysis as implemented in the BASIC program, St. George d'Orques, France (Raymond 1985). The correction for control mortality, which was always below 10%, was analysed with the same program using Abbot's formulae. The calculated LC50 values were considered different if their 95% confidence intervals (CIs) did not overlap. Because there had been a very low population density of black flies in PA over the past few years, the resistance ratios (LC50 of the resistant population/LC50 of the field-reference population) were calculated with the latest LC50 value recorded for the field-reference population. The mean esterase activities from both the individual resistant and field-reference populations were compared by non-parametric ANOVA (Kruskal Wallis) followed by Dunn's multiple comparison test. The mean GST activities were analysed by two-way ANOVA followed by Fisher's least significant difference test.



Toxicity assays - The concentration mortality lines for fenvalerate are shown in Fig. 1, together with complementary results from 1997 and 1999 that have been published elsewhere (Montagna et al. 1999, 2003). The FO population mortalities in 2002, 2005 and 2008 were 42% or less at the highest concentration of fenvalerate assayed (2.5 mg L-1 was the maximum soluble concentration) and subjected to a probit analysis. The mortality at the highest concentration of fenvalerate assayed was 38.5% in 2002, 42.3% in 2005 and 21% in 2008. These results indicated a small increase in the susceptibility to fenvalerate in the FO population collected in 2005 relative to 2002, followed by a decreased susceptibility in 2008; because a probit analysis could not be performed, the significance of this value is unknown. The LC50 and slope value for the field-reference population (PA) recorded in 2005 were 0.0045 mg L-1 and 3.1, respectively. Considering the entire monitoring period, including the previously published results from 1997 and 1999 (Montagna et al. 1999, 2003), a significant increase in fenvalerate resistance was observed in the FO population from 1997-2008. Three stages in the process of resistance development were apparent. At first, the LC50 values increased significantly from 0.15 mg L-1 in 1997 to 0.76 mg L-1 in 1999 (Table) and to even higher values in 2002, according to the probit analysis (Fig. 1). The resistance ratios at the LC50 level were 88 and 395 in 1997 and 1999, respectively (Table). During this stage, a shallow slope (1.4) was followed by a steep slope (3.2), suggesting an increase in homogeneity. Subsequently, there was a small initial increase in the susceptibility to fenvalerate in 2005 and a decrease in 2008.



The concentration mortality lines for deltamethrin are shown in Fig. 2 with complementary results from 1997 that have been published elsewhere (Montagna et al. 1999). The LC50 (mg L-1) and slope values (in parentheses) for deltamethrin for the FO population were 0.010 (4.5), 0.0052 (2.5) and 0.0065 (1.3) in 1999, 2002 and 2008, respectively. The LC50 value for the field-reference population collected in 1999 was 4.0 x 10-5 mg L-1. The resistance ratios at the LC50 level were 250, 130 and 162 for the sampling periods of 1999, 2002 and 2008, respectively. Considering the entire monitoring period, including the previously published results from 1997 (Montagna et al. 1999), the trend of deltamethrin resistance was quite similar to that observed for fenvalerate in the FO population (Figs 1, 2). The LC50 values significantly increased from 0.0027 mg L-1 in 1997 to 0.010 mg L-1 in 1999 and the slopes of the regression lines were shallow (2.0) and steep (4.5) in these two years, respectively (Table), suggesting an increase in the homogeneity towards resistance. The FO population was 90 and 250-fold more resistant at the LC50 level than the PA populations collected in 1997 and 1999, respectively. Subsequently, there was a non-significant decline in the LC50 value between 1999-2002, according to the CIs. Finally, there was a small increase in the LC50 value in 2008 that was significantly different from that in 1999, but not that in 2002. The LC50 values recorded for the field-reference population (PA) were 3.0 × 10-5 mg L-1 in 1997 and 4.0 × 10-5 mg L-1 in 1999; the differences were not significant.



The concentration mortality lines for azinphos methyl are shown in Fig. 3 with complementary results from the sampling periods of 1996 (Montagna et al. 1999) and 2005 (Anguiano et al. 2008). The LC50 (mg L-1) and slope values (in parentheses) recorded for the FO population for azinphos methyl were 0.024 (4.7) and 0.042 (6.4) in 2000. In contrast, the LC50 value for the field-reference population was 0.0090 mg L-1 in 2000, which, according to the CI, was significantly different from that of the resistant population. The resistance ratios at the LC50 level were 2.7 and 4.6 for the sampling periods of 2002 and 2008, respectively. Collectively, the new results and the previously published results from 1996 and 2005 (Montagna et al. 1999, Anguiano et al. 2008) indicate that the FO population exhibited a small but significant increase in azinphos methyl resistance from 1996-2002 compared with the field-reference population. The resistance ratios at the LC50 values were 1.7, 2.7 and 4.6 in 1996, 2000 and 2002, respectively. Conversely, the FO population exhibited a significant increase in the susceptibility to azinphos methyl from 2002 (0.042 mg L-1) to 2005 (LC50 = 0.021 mg L-1). In contrast to the response of the larvae from FO to pyrethroids, small changes in the regression slopes for azinphos methyl were observed during the sampling period. The LC50 values for the field-reference population (PA) ranged from 0.0068 mg L-1 in 1996 to 0.011 mg L-1 in 2005. There were no significant differences between the LC50 values calculated in 1996 and 2000. However, according to the confidence limits, there was a significant increase in the LC50 in 2005 relative to 1996 and 2000.



Enzyme activity - The general esterase activity from individual larvae in the resistant and field-reference populations, along with complementary results from the sampling periods of 1999 and 2005 that have been published elsewhere (Montagna et al. 2003, Anguiano et al. 2008), are illustrated in box-and-whisker plots in Fig. 4. The mean esterase activity ± standard deviation (SD) (µg min-1 mg-1) of the FO population in 2009 (2.85 ± 1.51) was significantly higher (p < 0.05) than that of the PA population in 2005 (0.86 ± 0.35) (Anguiano et al. 2008).



Considering the entire monitoring period, including the previously published results from 1999 and 2005 (Montagna et al. 1999, Anguiano et al. 2008), the average esterase activity in the resistant population consistently increased throughout the sampling period, although the differences between 2005 (2.17 ± 1.71 µg min-1 mg-1) and 2009 were not statistically significant. The mean activities in 1999 (1.29 ± 1.13 µg min-1 mg-1) and 2005 may be overestimated as a result of a few very high values. Indeed, the distribution of esterase activities of the FO population collected in 2009 exhibited a much smaller departure from normality (skewness = 0.72) than those measured in 1999 (skewness = 3.62) and 2005 (skewness = 3.31). The mean ± SD esterase activities (µg min-1 mg-1) in the field-reference population were 0.46 ± 0.25 in 1999 and 0.86 ± 0.35 in 2005 and the differences were not significant. The frequency of individuals from the resistant population with esterase activities higher than the maximum value observed in the PA population were 9.6% in 1999, 29.7% in 2005 and 55.8% in 2009.

The GST activities recorded from both populations in the present study and in a previous study (Montagna et al. 2003) are shown in Fig. 5 as box-and-whisker plots. The mean ± SD enzyme activity recorded for the field-reference population in 2005 (0.20 ± 0.0178 µmoles CDNB min-1 mg protein-1) was significantly lower (p = 0.011) than that determined in the resistant population during the same sampling period (0.23 ± 0.026 µmoles CDNB min-1 mg protein-1). Conversely, the mean ± SD enzyme activity determined for the field-reference population in 2005 was not significantly different (p = 0.76) from that recorded for the resistant population in 2009 (0.19 ± 0.021 µmoles CDNB min-1 mg protein-1). Unexpectedly, the mean GST activity of the FO population in 2009 was significantly lower (p = 0.005) than that of the 2005 collection. Moreover, the distribution of this enzyme activity in the FO population collected in 2009 exhibited a much smaller departure from normality (skewness = 1.47) than the population collected in 2005 (skewness = -3.05). Finally, both the previous (Montagna et al. 2003) and the present results demonstrated that the GST activities of the resistant population fluctuated over the years.




Adaptive evolutionary changes that occur within decades or less are defined as contemporary evolution. The development of resistance in response to intensive pesticide pressure is an example of this adaptive continuous evolution (Stockwell et al. 2003). The frequency of resistant genotypes increases in populations under insecticide pressure and the regression lines shift to the right with lower slope values (Brown & Pal 1971). As the selection pressure continues, increased LC50 and LC95 values associated with higher slopes are indicative of the progression of resistance to a higher intensity and frequency of resistant genotypes (Norris 1957, Immaraju et al. 1989). A subsequent decrease in the slope value would be indicative of an evolution of resistance to higher intensities (Immaraju et al. 1989). Increased LC50 values and slope changes have already been observed under laboratory and field insecticide selection in both insect (Georghiou et al. 1966, Georghiou & Hawley 1971, Sarkar et al. 2009) and mite populations (Sato et al. 2000).

The contemporary evolution of pesticide resistance in a field population is a complex, stepwise process influenced by genetic, biological/ecological and operational factors. Some genetic factors that contribute to the rapid development of resistance are the dominance, initial frequency and number of R alleles and the integration of R alleles with fitness factors. A high reproduction potential of the species associated with low mobility and a lack of untreated reservoirs are some of the biological/ecological factors that accelerate the evolution of resistance. The operational factors are related to both the chemicals and the application procedures. Among these factors, the development of resistance is favoured if the pesticide is persistent in the environment, the application rate is high and frequent, there is no chemical rotation and the insecticide pressure occurs in more than one life stage (Georghiou & Taylor 1986).

The rapid evolution of resistance to pyrethroids, principally fenvalerate, in black flies from FO observed in both the present and previous studies (Montagna et al. 1999, 2003) may be explained by both the nature of the FO population and the control strategies used against the codling moth. Among black flies from the study area, the following factors may be related to a high insecticide selection pressure. First, black flies have at least three generations per year and their life cycle overlaps with pesticide applications. In the laboratory, a shorter life cycle results in the faster development of insecticide resistance (Ko?išová et al. 1995). Second, there is no refuge for larvae; they remain in the same location for the entire larval stage and are unable to escape from pesticide applications that reach the irrigation channels by air drift and natural run-off. Groeters and Tabashnik (2000) concluded from simulation models that the delay of resistance increases as the refuge size increases. Third, black fly larvae feed on filtered particulate matter, in which pesticide accumulation and persistence are greater than in water. Wauchope (1978) and Schulz (2001) observed higher levels of organochlorine, organophosphate and pyrethroid insecticides in the suspended particles than in the water. Finally, adult black flies from FO may also be under insecticide pressure either during insecticide application or during rest through absorption of the chemical from fruit leaves. Regarding the operational factors involved in the rapid evolution of pyrethroid resistance during the first years of sampling, this family of insecticides (fenvalerate, deltamethrin, cypermethrin and lambda-cyhalothrin, among others) was introduced in 1982 and used extensively for almost two decades. Furthermore, traditional pest control programmes usually included in up to 10 applications of insecticides each growing season. Pyrethroids were subsequently restricted in the valley because they failed to control C. pomonella. Instead, azinphos methyl was principally recommended for pest management. Since 2005, acetamiprid, rynaxypyr, spinosad and other unconventional pesticides have been the main insecticides of choice and there are only a few applications of pyrethroids and azinphos methyl during each growing season. Modifications in the pesticide applications during recent years of sampling may explain the slight evolution of fenvalerate and deltamethrin resistance over this period. The shallow slope of the regression line of fenvalerate observed in the FO population in 2008 suggests a vast potential for the enhancement of the resistance levels. The resistance to azinphos methyl increased until 2002, with a subsequent reversion in 2005.

Previous work (Montagna et al. 2003) has suggested that target insensitivity and enzyme detoxification are involved in pyrethroid resistance. The use of the synergists piperonyl butoxide and S,S,S-tributyl phosphorotrithioate (DEF) has confirmed the primary contribution of oxidases and esterases to pyrethroid resistance. In the present study, the resistant population exhibited 2.5 (2005 collection) and 3.3-fold (2009 collection) higher mean esterase activities than the field-reference population in 2005. These and previous (Montagna et al. 2003) results indicate the involvement of these enzymes in pyrethroid resistance. Conversely, the mean GST activity of the resistant population collected in 2005 was only 1.15-fold higher than that of the field-reference population in the same collection year. Moreover, there were no significant differences between the mean GST activities of the resistant and the field-reference populations between 2009-2005, respectively. Taking into account previous results (Montagna et al. 2003), the mean GST activities in the resistant population were lower (1.15-fold) and higher (1.26-fold) than the field-reference population in 1996 and 1999, respectively; thus, the role of these enzymes in pyrethroid resistance in the FO population is negligible.

The enhanced GST activities observed in the FO populations collected in 1999 and 2005 and the subsequent decrease in 2009 may be associated with both the frequent and occasional use of azinphos methyl.

Pyrethroid resistance has been associated with increased GST and mixed function oxidase activities (Djouaka et al. 2011, Strong et al. 2008, Morgan et al. 2010) or GST and esterase activities (Munhenga et al. 2008) in mosquitoes. In contrast, increased GST activity has been associated with azinphos methyl resistance in two lepidopteran species (Suckling et al. 1990, Fuentes-Contreras et al. 2007). In black flies, higher levels of esterase activity (Magnin et al. 1987, Andrade & Branco 1990, Parker & Callaghan 1997) have been identified in organophosphate-resistant populations.

Recent studies suggest that esterases provide a mechanism of resistance that is reselected by the pesticides currently used to control fruit tree pests. Although mixed function oxidases are involved in the principal resistance mechanism against acetamiprid in Apis mellifera and spinosad in Spodoptera exigua, a significant synergism effect of DEF on both pesticides has also been demonstrated (Iwasa et al. 2004, Wang et al. 2006).

The present results showed that resistance to pyrethroids in the FO population has evolved very rapidly during the period in which these pesticides were extensively applied to control C. pomonella and other fruit pests. Following the introduction of unconventional pesticides, fenvalerate and deltamethrin resistance reached a relatively steady state and subsequently increased. The levels of resistance to azinphos methyl were low over the survey period, regardless of the massive use of this pesticide over a five-year period. Esterase activity is involved in one of the mechanisms underlying the high levels of pyrethroid resistance in black flies. These enzymes may be reselected by currently used pesticides and the increased activity of these enzymes enhances the pyrethroid resistance that has been observed recently.

In response to increasing populations of black flies, the government of Argentina initiated a pilot programme in 1991 to evaluate the effectiveness of larval control in irrigation channels and drainage ditches with B. thuringiensis israelensis (Vectobac AS). Although most trials resulted in effective larval mortality, the projected cost of the black fly suppression programme in the Río Negro Valley with this method was very expensive (Gray et al. 1999). To efficiently decrease black fly populations in this area at a lower cost than biological control alone, an array of strategies should be implemented. First, the breeding sites must be decreased by the systematic and mechanical removal of channel vegetation, which serves as a substrate for the immature stages. Second, the black fly population densities must be monitored so that treatment with B. thuringiensis toxins can be administered at the peak density. Finally, both the fruit-pest and black fly chemical controls must be coordinated. In agreement with the final recommendation, further studies will focus on the evaluation of black fly sensitivity to more selective insecticides, such as neonicotinoids and the insect growth regulators that are currently in use.



To Guillermo Sabino, Department of Statistic, Facultad de Economía y Administración, for the suggestion in the statistical analysis.



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Received 24 July 2011
Accepted 14 March 2012
Financial support: UNCOMA Projects (04/I701, 04/I940, 04/I004), FONCYT (PICT-2007-00214-00-01)

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