Mem Inst Oswaldo Cruz, Rio de Janeiro, 96(5) July 2001
Biogeography of Triatominae (Hemiptera: Reduviidae) in Ecuador: Implications for the Design of Control Strategies
Pathogen Molecular Biology and Biochemistry Unit, Department of Infectious and Tropical Diseases, London School of Hygiene and Tropical Medicine, Keppel St., London WC1E 7HT, UK
IUnidad de Medicina Tropical, Instituto `Juan César García', Quito, Ecuador
IIUnidade de Parasitologia Médica-Patologia, Faculdade de Medicina, Universidade de Brasília, DF, Brasil
IIIInstituto Nacional de Higiene y Medicina Tropical `Leopoldo Izquieta Pérez', Quito, Ecuador
Chagas disease control strategies strongly depend on the triatomine vector species involved inu00a0Trypanosoma cruzitransmission within each area. Here we report the results of the identification of specimens belonging to various species of Triatominae captured in Ecuador (15 species from 17 provinces) and deposited in the entomological collections of the Catholic University of Ecuador (Quito), Instituto Oswaldo Cruz (Brazil), the Natural History Museum London (UK), the London School of Hygiene and Tropical Medicine (UK), the National Institute of Hygiene (Quito), and the Vozandes Hospital (Quito). A critical review of published information and new field records are presented. We analysed these data in relation to the life zones where triatomines occur (11 life zones, excluding those over 2,200 m altitude), and provide biogeographical maps for each species. These records are discussed in terms of epidemiological significance and design of control strategies. Findings relevant to the control of the main vector species are emphasised. Different lines of evidence suggest thatu00a0Triatoma dimidiatau00a0is not native to Ecuador-Peru, and that synanthropic populations ofu00a0Rhodnius ecuadoriensis in southern Ecuador-northern Peru might be isolated from their sylvatic conspecifics. Local eradication of T. dimidiatau00a0and theseu00a0R. ecuadoriensisu00a0populations might therefore be attainable. However, the presence of a wide variety of native species indicates the necessity for a strong longitudinal surveillance system.
Around 3 million people live under risk conditions for Trypanosoma cruzi transmission in Ecuador; prevalence estimates indicate that ~150,000 people are already infected (Aguilar et al. 1999). Sixteen triatomine species have been reported from the country (excluding doubtful records of Triatoma infestans and Rhodnius prolixus) (Aguilar et al. 1999). At least 13 of these species (see Tables I-III) are actual or potential vectors of Chagas disease (Lent & Wygodzinsky 1979, WHO 1991, Abad-Franch 2000). This complex situation is currently being investigated in the context of the National Programme for Chagas Disease Control in Ecuador. Our aim is to contribute to these efforts by analysing and completing the relevant information about Chagas disease triatomine vectors in Ecuador.
From 1998 to 2000, and as part of our research on the epidemiological significance of Rhodnius species in Ecuador and Peru, we undertook a revision of the Triatominae kept at various important entomological collections. During that revision, new data on distribution of some species in Ecuador became apparent. We added entomological records from our own fieldwork and from research being carried out by Ecuadorian colleagues. Here we report those new records, together with previously published data, and analyse them in relation to the main ecological and epidemiological traits of the different species. Finally, recommendations on vector control strategies are put forward.
MATERIALS AND METHODS
For this study, we reviewed available published reports, and the specimens belonging to the subfamily Triatominae deposited at the Invertebrate Museum of the Catholic University of Ecuador, Quito, the Herman Lent and Rodolfo Carcavallo Collections (Laboratório Nacional e Internacional de Referência em Taxonomia de Triatomíneos, Departamento de Entomologia, Instituto Oswaldo Cruz, Rio de Janeiro, Brazil), the Natural History Museum, London (UK), the London School of Hygiene and Tropical Medicine (UK), the Vozandes Hospital (Quito, Ecuador), and the National Institute of Hygiene and Tropical Medicine (Quito, Ecuador). Fieldwork and unpublished records were also included in our analysis.
Notes on epidemiological significance of each species were prepared on the basis of published information, unpublished reports, and field observations. For geographical information, we used the guide by Miranda (1995), the "Índice Toponímico" of the Instituto Geográfico Militar (IGM 1978-82, 1982-96), and cartographic material provided by the IGM. Life zones were established following the ecological maps proposed by Cañadas (1983) and Cañadas and Estrada (1978, cf. Dodson & Gentry 1991), based on the life zones described by Holdridge (1967). We included life zones under 2,200 m altitude in the analysis. In the distribution maps (Figure), marks indicate places of capture. Life zones where each species occur are light grey, and we added the outline and number of the life zones representing the potential distribution of each species (areas from where no records exist, but where ecological features are identical to other zones where captures have been made).
Results on geographical and ecological distribution of species are shown in the Figure and in Tables I-III; 17 out of 21 provinces have produced records of triatomines (excluding doubtful reports from two more provinces). The studied species occupy 11 life zones in Ecuador. Life zones in the Andes range (2,200-6,310 m altitude) were not included in the analysis; apparently, only T. carrioni occurs there. Annual rains in areas where triatomines occur range between 62.5-125 mm/year in the tropical desert and 2,000-4,000 mm/year in the wet and moist forests (Table IV). Average temperatures ranged from 12-18ºC in the low montane forest areas to 24-26ºC in the coastal dry tropical forests (Table IV). Altitude range was 0-2,650 m (Tables I, IV). The maximum number of species recorded in a single life zone corresponds to the Amazon rainforest (seven species, excluding unconfirmed records of T. dimidiata and R. ecuadoriensis). These two latter species, deemed the main Chagas disease vectors in the country, have the widest distribution range; T. dimidiata has been reported from six different life zones in the country and R. ecuadoriensis from five (see Tables I, II, IV). The distributions of these and all the other species in relation to life zones are also summarised in Table IV.
No records from the Galápagos Islands were found.
*New field records were obtained after the preparation of the manuscript (province of Pichincha, life zone 9): Triatoma dimidiata (domestic colony), Rhodnius ecuadoriensis (adults in house), and Panstrongylus rufotuberculatus (adults in houses).
Complementary sampling and further analysis are indispensable to achieve an accurate idea of how triatomines are distributed in Ecuador, the way they are related to different ecological zones, their synanthropic behaviour, and their inter- and intra-specific relations. Records from some provinces are limited or do not exist. The ecological complexity of Ecuador is illustrated in the diversity of life zones (from desertic areas to pluvial forests). The high number of triatomine species also reflects such diversity.
T. dimidiata occurs only in low, dry areas of the coast, including the tropical desert in the Santa Elena peninsula (Guayas), and seems to be always in a domestic habitat. Only one report of adult specimens found in an allegedly sylvatic environment (under the bark of a dead tree) (cf. Zeledón 1981) was found. However, the actual presence of sylvatic colonies of this species in Ecuador has never been documented; specimens found in peridomestic terrestrial bromeliads and periurban rubbish dumps in Manabí (Vector Control Service, unpublished observations) cannot be considered as truly sylvatic. This fact, together with the apparent discontinuity in the distribution of the species from Mexico to Ecuador (absent from southern Colombia, except in some localities of the upper Magdalena valley) (Zeledón 1981, D'Alessandro & Barreto 1985, Carcavallo et al. 1999), makes us contemplate the hypothesis that it was introduced into coastal areas of Ecuador and Peru. Sea trade is known to have linked Mesoamerican and Ecuadorian-Peruvian cultures from ~1500 BC (Meggers & Evans 1963). As pointed out by Schofield et al. (1999), genetic and phenetic simplification generally impedes the re-adaptation of strictly domestic triatomines to new, unstable sylvatic habitats. If the introduction of such T. dimidiata populations to Ecuador-Peru is confirmed, meaning that no sylvatic populations ofT. dimidiata occur in Ecuador, then the species might be a suitable target for local eradication (pyrethroid insecticide spraying of all dwellings in positive localities is recommended in such a situation) (Acevedo et al. 2000, Schofield 2000). Preliminary results of nuclear and mitochondrial gene sequencing (Bargues et al. 2000, Marcilla et al. 2001, Solís-Mena et al. unpublished data) and morphometry (Solís-Mena et al. 2000) are lending support to this hypothesis. Recently, threeT. dimidiata adults were allegedly collected in a dwelling in the Ecuadorian Amazon; however this finding needs further confirmation.
R. ecuadoriensis colonises human environments in central and southern Ecuadorian provinces west of the Andes, and in northern Peru. Sylvatic populations seem primarily associated with the endemic Phytelephas aequatorialis palm trees in the central coastal region (Romaña et al. 1994, Avilés et al. 1995a, Abad-Franch et al. 2000). We recently found 27% of 64 P. aequatorialis palms to harbour R. ecuadoriensis breeding colonies in three provinces of the Pacific slope of the Andes (Abad-Franch 2000); both invasion and colo-nisation of human habitats by wild insects have been documented in coastal Ecuador (Defranc 1987, Abad-Franch 2000). Treatment of infested dwellings and monitoring of re-infestations should be the recommended control strategy there. We also studied the presence of R. ecuadoriensis in temperate valleys of the provinces of Loja and El Oro (near the Peruvian border). Palm trees are completely absent in the studied areas, probably due to massive deforestation that occurred in the last 30-40 years (Dodson & Gentry 1991). Nine percent of 118 dwellings surveyed in two communities were infested (crowding indices from 42 to 78), with the majority of colonies breeding in peridomestic chicken coops, but also inside houses _ mainly in beds and mud walls (Abad-Franch 2000). It is of greater importance for the control of this species in southern Ecuador and northern Peru to determine whether sylvatic populations still occur there (making re-infestation likely), or if domestic insects have become isolated from their wild conspecifics as a consequence of deforestation (local eradication could be attainable in this case). We have also detected the presence of strictly wild R. ecuadoriensis forms in northern Ecuador; their specific status needs however to be confirmed (Abad-Franch 2000, Abad-Franch et al. 2000). Finally, we found two specimens labelled as collected on the eastern slope of the Andes (marked as uncertain data on the map, as we suspect erroneous places of capture indicated on labels).
T. carrioni, an endemic species that has adapted to human habitats in the Andean valleys of southern Ecuador and northern Peru, occupies a wide range of life zones (dry and humid, 1,000-2,650 m altitude) and has been reported to feed on humans and horses (Lent & Wygodzinsky 1979). An adult specimen was recently captured by light trapping in the northern province of Pichincha. A nymph apparently belonging to this species was captured in an epiphytic bromeliad in the canopy of primary cloud forest in a neighbouring area (Figure, Table I). In the southern Andean provinces of Loja and Azuay, the species has been found in human-related habitats both in rural and urban areas (León 1949, Espinoza 1955, Defranc 1982). Some capture places (marked with + in the Figure) are located in Andean life zones over 2,200 m; data available indicate that the species has only been found there in human environments, but this does not preclude its presence in wild habitats as well. Control of this species should contemplate the possibility of re-infestations from wild populations; treating of infested homes and a strong surveillance component must therefore be recommended.
R. pictipes and R. robustus are recorded from the Ecuadorian Amazon _ where seropositivity ranges from 0.8% to 6% (cf. Aguilar et al. 1999). We recently studied their presence in palm trees in the Ecuadorian Amazon region. Forty-six percent out of 56 palms surveyed were positive, including five genera (Attalea, Astrocaryum, Oenocarpus, Phytelephas,and Elaeis) (Palo-meque et al. 2000). Several specimens labelled as R. robustus collected in western Ecuador (Loja and Los Ríos), are deposited at the H. Lent Collection (Instituto Oswaldo Cruz). This finding is most likely related to erroneous capture sites indicated on labels. Our investigations confirm that R. stali, a synanthropic species close to R. pictipes (Lent et al. 1993), is not known in the Ecuadorian Amazon.
P. rufotuberculatus is truly domestic in some areas of southern Ecuador, where breeding colonies have been found inside dwellings (Avilés et al. 1995b, Abad-Franch 2000). Similar behaviour has also been reported from Bolivia (Noireau et al. 1995, Dujardin et al. 1998) and Peru (Lizaraso 1955, Calderón et al. 1985). Adult insects may also invade houses attracted to electric light (Lent & Wygodzinsky 1979, Salomón et al. 1999). The epidemiological significance of this species deserves further research in southern Ecuador. The possibility that this species colonises houses after domiciliated species are eliminated by control interventions has to be taken into account by control managers. The species occurs mainly in low, dry areas, but may also be found in zones of very humid premontane forest in northern Ecuador, where it is sylvatic but has been captured in houses when flying attracted to light.
P. geniculatus is broadly distributed throughout the continent, and occurs on both slopes of the Andes. Specimens from the Ecuadorian Amazon and coastal regions display conspicuous, apparently constant chromatic differences. The species has been involved in disease transmission in the Ecuadorian Amazon foci (cf. Aguilar et al. 1999). It seems to be readily attracted to electric light (Lent & Wygodzinsky 1979), and will also approach oil candles in the Ecuadorian Amazon (FS Palomeque, pers. commun.). Peridomestic colonies have been reported from the Brazilian Amazon (Valente et al. 1998, Valente 1999), but reports of domiciliation in Ecuador (Amunárriz 1991, Chico et al. 1997) need confirmation. The species is to be considered as a potential secondary vector in its distribution areas.
P. howardi, a little known species endemic to a dry area of Manabí, is quite commonly found entering human dwellings _ as adult specimens, except for one report of a breeding colony in a peridomicile (Defranc 1982). Its sylvatic habitats and hosts remain unknown. The possibility that P. howardi transmits T. cruzi to people by colonising or invading human-related structures points to the necessity for entomological studies of this species.
P. chinai probably also plays a role in the wild cycle of T. cruzi transmission in some areas of southern Ecuador and northern Peru, but only few data are available. It has been found to breed in chicken coops and, occasionally, in human dwellings. Adults may be attracted to artificial light (Lent & Wygodzinsky 1979). The species may also behave as a secondary vector, thus entomological surveillance is a key for the success of control activities.
P. herreri has only been reported once from Ecuador (Aguilar et al. 1999). It is domestic in northern Peru, where it is the main vector of Chagas disease (Herrer 1956, 1977, Lent & Wygodzinsky 1979, Calderón et al. 1985). We recently identified a female P. herreri captured in a dwelling of an indigenous village in the province of Napo, confirming our previous record. We also examined a P. lignarius female (captured in primary rainforest) which has some mixed characters of P. lignarius and herreri. These closely related species showed reproductive compatibility under laboratory conditions (Barrett 1988), but no hybrids have been reported from nature (Lent & Wygodzinsky 1979). Their taxonomic status needs to be clarified as it has epidemiological implications. The only previous record of P. lignarius in Ecuador (in the Andean highlands city of Cuenca, province of Azuay) (Rodríguez 1959) may be due to misidentification with P. herreri, or to an erroneous capture site indicated on the label.
Other Triatominae species (T. dispar, T. venosa, Eratyrus mucronatus, E. cuspidatus and Cavernicola pilosa) seem to have little or no epidemiological significance in Ecuador; Figure and Table I show the main trends. Three of them (T. venosa, E. cuspidatus, and E. mucronatus) have however been reported to show some degree of synanthropism in different countries (Lent & Wygodzinsky 1979, D'Alessandro & Barreto 1985, Noireau et al. 1994), but seem to be mainly sylvatic in Ecuador.
The Ministry of Public Health is currently developing the strategy for the control of vector-borne Chagas disease in Ecuador. It will be based on updated information about the distribution and synanthropic behaviour of different triatomine species. The presence of a wide variety of them (~12% of all recognised species, and ~18% of South American species), in their majority present in wild environments, will be one of the main difficulties. Only one of these species, T. dimidiata, may be suspected of having been artificially introduced and therefore susceptible to eradication. The possibility that some southern domestic populations of R. ecuadoriensis are isolated from wild foci must be ascertained; if so, local elimination might also be attainable. Autochthonous species may behave as secondary vectors, occupying empty niches when domestic triatomines are eliminated by insecticide spraying. Various species are in their way to true domestication, while others show ability to invade houses without establishing breeding colonies there. A strong component of longitudinal vigilance with community involvement is recommended in such situations, complementing the use of residual pyrethroids (Dias 1991, Dias & Schofield 1999, Acevedo et al. 2000, Schofield 2000). This work aims to be a contribution to the development of the technical basis for the National Control Programme currently in preparation (including definition of risk areas, sero-entomological surveys, spraying interventions, and the establishment of longitudinal surveillance systems), and to provide researchers and public health authorities with baseline knowledge indispensable for the design of adequate strategies.
To CJ Schofield and J Jurberg for their help during the preparation of this work. To AG Guevara (Vozandes Hospital, Quito) and J Racines V (National Institute of Hygiene, Quito) for providing us with entomological records from their fieldwork, and to G Onore and M Webb for permitting us to review the material deposited at the Invertebrate Museum of the Catholic University of Quito and the Natural History Museum (London), respectively.
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