The population structure of Glossina fuscipes fuscipes in the Lake Victoria basin in Uganda: implications for vector control
- Chaz Hyseni†1Email author,
- Agapitus B Kato†2, 3,
- Loyce M Okedi4,
- Charles Masembe2,
- Johnson O Ouma5,
- Serap Aksoy6 and
- Adalgisa Caccone1
© Hyseni et al.; licensee BioMed Central Ltd. 2012
Received: 16 May 2012
Accepted: 15 September 2012
Published: 4 October 2012
Glossina fuscipes fuscipes is the primary vector of trypanosomiasis in humans and livestock in Uganda. The Lake Victoria basin has been targeted for tsetse eradication using a rolling carpet initiative, from west to east, with four operational blocks (3 in Uganda and 1 in Kenya), under a Pan-African Tsetse and Trypanosomiasis Eradication Campaign (PATTEC). We screened tsetse flies from the three Ugandan PATTEC blocks for genetic diversity at 15 microsatellite loci from continental and offshore populations to provide empirical data to support this initiative.
We collected tsetse samples from 11 sites across the Lake Victoria basin in Uganda. We performed genetic analyses on 409 of the collected tsetse flies and added data collected for 278 individuals in a previous study. The flies were screened across 15 microsatellite loci and the resulting data were used to assess the temporal stability of populations, to analyze patterns of genetic exchange and structuring, to estimate dispersal rates and evaluate the sex bias in dispersal, as well as to estimate demographic parameters (NE and NC).
We found that tsetse populations in this region were stable over 4-16 generations and belong to 4 genetic clusters. Two genetic clusters (1 and 2) corresponded approximately to PATTEC blocks 1 and 2, while the other two (3 and 4) fell within PATTEC block 3. Island populations grouped into the same genetic clusters as neighboring mainland sites, suggesting presence of gene flow between these sites. There was no evidence of the stretch of water separating islands from the mainland forming a significant barrier to dispersal. Dispersal rates ranged from 2.5 km per generation in cluster 1 to 14 km per generation in clusters 3 and 4. We found evidence of male-biased dispersal. Few breeders are successfully dispersing over large distances. Effective population size estimates were low (33–310 individuals), while census size estimates ranged from 1200 (cluster 1) to 4100 (clusters 3 and 4). We present here a novel technique that adapts an existing census size estimation method to sampling without replacement, the scheme used in sampling tsetse flies.
Our study suggests that different control strategies should be implemented for the three PATTEC blocks and that, given the high potential for re-invasion from island sites, mainland and offshore sites in each block should be targeted at the same time.
The tsetse fly (Glossina) is a major vector of trypanosomiasis throughout sub-Saharan Africa, causing extensive morbidity and mortality in humans and livestock [1, 2]. It has been estimated that economic benefits to Africa from the eradication of tsetse could reach US$4.5 billion per year. Currently, no vaccines exist to prevent the disease and available drugs to treat HAT are expensive, can cause severe side-effects, and are difficult to administer in remote villages . As a consequence, an effective alternative for controlling the disease is to target the tsetse vector [4, 5]. A variety of methods to control tsetse populations are available, including habitat modification around homesteads, trapping, insecticide-treated targets, insecticide-treated cattle, and aerial or ground spraying. The release of sterile or transgenic insects has been either used or proposed as an additional control measure [4–9]. Tsetse control is implemented using two strategies: eradication and suppression. Eradication aims at eliminating fly populations from a given area, while the objective of suppression is to greatly reduce population size.
Genetic data provide a powerful tool to help identify appropriate vector control strategies, as they can be used to estimate spatial and temporal differentiation of populations, and patterns and extent of migration. These data, together with ecological and environmental, data can be used to customize vector control efforts according to local conditions and species in order to determine whether eradication or suppression is appropriate [10, 11]. For example, studies of tsetse in Burkina Faso, Guinea and Senegal have identified populations that are sufficiently isolated to warrant attempts at complete eradication [10–12]. Studies elsewhere have documented relatively high levels of gene flow, necessitating integration of barriers into eradication schemes [13, 14], or warranting an area-wide control effort that encompasses populations linked by gene flow [15, 16]. Regional studies such as the one on G. palpalis palpalis in west and central Africa  have provided information that is useful for control efforts at a regional scale. Other population genetic studies have pointed to specific populations at a local level where control and detection methods need improvement .
In 2001, the Organization for African Unity (OAU) launched a new initiative, the Pan-African Tsetse and Trypanosomiasis Eradication Campaign (PATTEC) to eradicate the tsetse flies from a vast area of sub-Saharan Africa (~10 million km2, seven Glossina species) by first reducing populations using area-wide approaches (odor-baited traps, insecticide-treated targets, pour-ons and ultra-low-volume aerial spraying), followed by massive release of sterile males to ensure eradication . In Uganda, phase I of this initiative has been initiated in the Lake Victoria basin, which is infested with Glossina fuscipes fuscipes (Gff). A program (Farming in Tsetse Controlled Areas, FITCA), which ended in 2004, reduced tsetse populations by 75% to 90% in the mainland sites of the target area, but the program did not include islands . By 2009, a PATTEC baseline survey revealed that mainland tsetse populations had rebounded to the high levels prior to the FITCA initiative .
We used genetic variation at 15 microsatellite DNA loci to examine the genetic differentiation of Gff populations within and between the three Ugandan PATTEC blocks. We used these data to estimate effective population size (NE), to evaluate temporal stability over 4-16 generations, and to measure genetic exchange and dispersal rates within and between blocks. In view of the finding that high levels of genetic exchange occur among continental Ugandan populations of Gff separated by distances smaller than 100 km , we embarked upon an investigation of gene flow patterns at a finer scale and used the results to assess the validity of the PATTEC operational blocks with respect to vector control, to provide suggestions regarding control strategies in each block, and to evaluate the possibility of using Gff island populations for eradication trials.
Sample collection information and genetic summary statistics
Seasonal and Total
(a) New sites for this study
(b) Sites from previous studies
DNA was extracted from tsetse legs using the PrepGEM Insect DNA extraction kit (ZYGEM Corp Ltd, Hamilton, New Zealand) as per the protocol provided by the manufacturer. We collected genotypic data across 18 microsatellite loci (see Additional file 1: Supplementary Material for technical details), including the 13 loci used in Beadell et al. . The other 5 (GmmA06, GmmB20, GmmD15, GmmL03, GmmL11) were selected among the loci described in Hyseni et al. . Due to low amplification and scorability of large alleles, locus Pgp17 was excluded from all analyses. We also excluded locus GpC5b, because it was monomorphic for all populations, excepting BZ and NS (in both cases, FIS = 1), and locus GmmD15, because it was monomorphic in all of the 11 sites we sampled. Thus, we only used 15 loci for all subsequent genetic analyses.
We used Genepop 4.1 to test for deviation from Hardy-Weinberg equilibrium (HWE) and also test for linkage disequilibrium (LD). For loci with fewer than four alleles, the complete enumeration method  was used. All other loci were tested using the Guo and Thompson  Markov chain method with 100,000 dememorizations, 1,000 batches and 10,000 iterations per batch. We also used Genepop to carry out global tests across loci for heterozygote deficiency and heterozygote excess. Significance values were adjusted for multiple testing (HWE) and comparisons (LD) using the Benjamini-Hochberg method  with a false discovery rate of 0.05. Summary statistics, including allele frequencies, allelic richness, observed heterozygosity (HO), expected heterozygosity (HE) and the inbreeding coefficient (FIS) were calculated using the program Genalex 6.41. In order to assess the statistical significance of genetic differentiation between temporal samples, we used Genepop to perform Fisher’s exact test on both microsatellite alleles and genotypes.
We used the model-based Bayesian clustering method implemented in Structure 2.3.3 to determine the genetic structure present among Gff populations in the Lake Victoria basin (details in Additional file 1: Supplementary Material). In addition to the Bayesian clustering implemented in Structure, we used a two-tiered multivariate ordination analysis, which makes no assumptions about deviations from Hardy-Weinberg and linkage equilibrium. This multivariate procedure, discriminant analysis of principal components (DAPC), has been shown to perform better than the Bayesian clustering approach when hierarchical and clinal structure is present in the data . We used the adegenet package  in R  for the DAPC (details in Additional file 1: Supplementary Material).
In order to quantify the genetic heterogeneity of Lake Victoria populations, we computed pairwise FST values  among sampling localities and among genetic clusters. FST values were obtained using the program Arlequin 3.5 and their significance computed via 10,000 permutations. FST describes the genetic structure produced by non-random distribution of individuals among subpopulations relative to the total population. However, our sample may contain multiple hierarchical levels of genetic differentiation, such as genetic clusters of populations with further partitioning within clusters, including potential genetic structure arising from isolation of island from mainland populations. In order to determine the contribution of different hierarchical levels to the observed genetic structure, we estimated hierarchical F-statistics using the method described in Yang  (details in Additional file 1: Supplementary Material) and implemented in the R package hierfstat.
To determine whether the genetic heterogeneity of Gff around Lake Victoria could be attributed to differences in dispersal ability between male and female flies, we performed t-tests on pairwise relatedness between individuals within genetic groups. Relatedness was computed using maximum likelihood estimation  implemented in Kingroup 2. Sex-biased dispersal was also assessed using three tests  implemented in Fstat 2.9.4 (details in Additional file 1: Supplementary Material).
Isolation by distance (IBD) and dispersal were evaluated using Rousset’s procedure  within genetic groups, using both a one-dimensional (1D) and a two-dimensional (2D) stepping-stone model. We compared the two models in order to determine differences in dispersal ability along Lake Victoria depending on whether movement happens along a line or across a surface (details in Additional file 1: Supplementary Material).
We used two methods to test for individual migrants between geographically neighboring genetic clusters (clusters 1 and 2, clusters 2 and 3, and clusters 3 and 4). In the first approach, we used the software Geneclass 2.0 to compute the likelihood of individual assignment based on regional allele frequencies [50, 51]. In the second approach, we used Flock 2.0 to assign genetically similar individuals to k partitions (details in Additional file 1: Supplementary Material).
We estimated effective and census population sizes for each genetic group. The geographic distance between the genetic groups should reduce the bias in estimation of effective population size (NE) that could be introduced by migration, which influences linkage disequilibrium as well as temporal methods of NE estimation . NE was computed using Waples and Do’s LD method implemented in the program LDNe. We also used two temporal methods to estimate NE: 1) a Bayesian algorithm based on coalescence and implemented in the program TM3 and 2) a pseudo-likelihood method  implemented in MLNE. Census size (NC) was computed via a sequential Bayesian method  adapted from Gazey and Staley  using an R software script . This method applies to a sampling scheme with replacement (non-invasive genetic sampling). Tsetse sampling, however, was done without replacement. We designed a method to account for the difference in sampling, which allowed us to utilize the adapted Gazey-Staley method [57, 58] to estimate NC (details in Additional file 1: Supplementary Material).
We observed the lowest HO and HE values in KG (0.29 and 0.30, respectively) and the highest in OK (0.54 and 0.53, respectively), while mean allelic richness across the 15 loci ranged from 2.87 in MA to 5.40 in BU (Table 1). The highest FIS value was observed in KO (0.187). After applying the Benjamini-Hochberg false discovery rate procedure  to the multiple testing of HWE, significant deviation from HWE was only observed in KO, which was due to significant heterozygote deficit. After applying the same correction for multiple comparisons of linkage between loci, no evidence of significant LD was found.
We examined the temporal stability of the samples for which temporal collections were available. Pairwise FST values between different sampling seasons revealed temporal homogeneity, i.e. temporal samples from the same sites were not significantly genetically differentiated. The smallest difference was observed between BU seasonal samples (FST = -0.001, P = 0.63) and highest in BY (FST = 0.003, P = 0.24). This was consistent with the similarity in allele frequencies between seasons observed in Additional file 2: Figure S1. We also carried out Fisher’s exact test on microsatellite alleles and genotypes and found no significant differences between temporal samples ( Additional file 3: Table S1).
Patterns of genetic differentiation
(a) Entire sample
(b) Cluster 1
(c) Cluster 2
(d) Cluster 3
Dispersal and migration
Clusters 3 & 4
Population size, migration and dispersal estimates
Clusters 3 & 4
N E /N C
σ 2 (km 2 )
Based on LDNe estimates
Clusters 3 & 4
Estimates of population size were computed for each genetic group. Table 4 shows effective population size (NE) estimates computed using both a linkage disequilibrium method (LDNe) and two temporal methods (a likelihood approach implemented in MLNE and a Bayesian approach implemented in TM3). Table 4 also reports the estimated census size (NC).
NE and NC were estimated for a dataset consisting of 12, 4, and 16 generations of flies from groups 1, 2 and 3, respectively. For the temporal methods only the first and the last samplings were used for NE estimation, as the increased sampling interval might decrease the bias caused by overlapping generations and age structure . With the exception of flies in group 1, the estimates obtained with the LDNe and temporal methods were very similar (Table 4). The lower temporal estimates for group 1 could be due to the higher substructure (FST between EB and other populations in the region was 0.07-0.09). We used NE estimates obtained via the LD method to calculate dispersal. NC was much higher in group 3 (4,121; Table 4) than elsewhere (1,199 in group 2 and 1,299 in group 1). The NE/NC ratio was lowest (0.075) in group 3; this ratio was higher in group 2 (0.101) and highest in group 1 (0.121).
The genetic data we collected for 14 sampling sites (Table 1 and Figure 1), which span up to 16 generations, showed that Gff populations are genetically stable over multiple seasons. Recent work on mainland sites in Uganda on the same species corroborates this result . The significant genetic non-differentiation over several generations seems counterintuitive, given seasonal fluctuations in Gff abundance [61, 62]. If this fluctuation is due to actual population reduction, however, 16 generations might not be enough time for genetic drift to produce differentiation, even at low NE values (33–310 individuals), especially if migration alleviates the effects of drift. Seasonal fluctuations in population size could also be a reflection of the low efficiency of trapping devices used to monitor fly populations . Gff is susceptible to high temperatures  and is known to inhabit the most humid habitats [65, 66]. The reduced fly catches during the dry season could thus be due to refuge-seeking behavior whereby flies hide under bushes that cannot be easily accessed by traps. This behavior is shared by other riverine tsetse species [67, 68]. Reduced movement during the dry season has been reported for G. tachinoides in northern Nigeria, which, like Gff, belongs to the palpalis group .
At the offshore island sites BY, BZ, and LI (Table 1), where temperatures are constantly lower and humidity is relatively high due to high rainfall and high evaporation rates throughout the year , dry and wet season fly catches are comparable in size. An exception to this is the low dry season tsetse abundance on the Buvuma islands (BV; Table 1). Strong dry-season winds, which are known to impact Gff activity [71, 72] and commonly occur on Buvuma, might be responsible for the low fly densities recorded there. Windy conditions have also been reported to affect tsetse movement in Nigeria . Additionally, given the genetic similarity between flies on the Buvuma islands and flies found in BY, BZ and LI, it is likely that Buvuma flies seek respite in adjacent habitats from harsh local dry season conditions.
Patterns of genetic differentiation and dispersal within and between clusters
Clustering (Figure 2) and multivariate (Figure 3) analyses detected four genetic clusters of tsetse populations in the Ugandan Lake Victoria basin. Based on DAPC (Figure 3), FST ( Additional file 4: Table S2), hierarchical F-statistics (Table 2) and IBD analyses (Figure 4), levels of genetic differentiation varied among clusters; while flies from clusters 1 and 2 were genetically distinct from each other and flies from clusters 3 or 4, the latter two clusters exchanged a large amount of genetic information. This was also confirmed by individual likelihood assignment tests, which identified numerous migrants (26 to 56) between clusters 3 and 4 (Figure 5). Clusters 1 and 2 (i.e., groups 1 and 2) correspond approximately to blocks 1 and 2, respectively, which were identified by PATTEC for eradication and suppression. However, two sites in block 1 are genetically closer to sites from block 2 (Figure 1). Clusters 3 and 4 (i.e., group 3) fall within block 3 targeted for initial monitoring in the first phase of the rolling carpet initiative.
The high level of genetic connectivity between the two easternmost clusters (clusters 3 and 4) could be facilitated by the presence of suitable Gff habitat, i.e., riparian and lacustrine thickets, tree canopies with understory vegetation, or patches of banana and Lantana camara[74–76]. These thickets have been greatly reduced through human settlement and other human activities in the areas that make up clusters 1 and 2. The higher level of isolation of tsetse flies observed in cluster 1 could be a function of increased habitat fragmentation and the intensive tsetse control activities dating back to the 1960s. In this area, high levels of deforestation have left only small gallery forests along the lakeshore. The growth of the city of Kampala could be an additional physical barrier to gene flow between flies from clusters 1 and 2. Increasing habitat fragmentation caused by human encroachment has been reported to have a major impact on the distribution, densities and structuring of riverine tsetse species [13, 77, 78].
Within clusters, island populations were not genetically differentiated from the mainland ones (Table 2 and Additional file 3: Table S1). Thus, the water body separating island and mainland sites (cluster 1: 19.9 km; cluster 2: 25.5 km; cluster 3: 34.4 km) does not act as a barrier to gene flow. Frequent human movements between islands and the mainland (fishing boats and daily ferry transport) may contribute to passive dispersal . The extent of genetic connectivity of fly populations in this study is congruent with the general finding of other genetic studies on Gff[16, 26] and other riverine species of tsetse [13, 14, 17, 80]. In G. p. gambiensis, however, Solano et al. report very low levels of migration between coastal sites and the Loos islands, situated 30 km off the coast of Guinea. Although this distance is not considerably greater than the distance separating adjacent island and mainland sites in our study (19.9-34.4 km), the differences in gene flow may be attributable to differences in the intensity of boat traffic, and thus more opportunity for passive dispersal of tsetse in the Lake Victoria region than off the coast of Guinea.
Population size and dispersal
Population size estimates were calculated for three groups, which we defined as genetically distinct units using multiple analyses. The effective population size estimates (NE) were quite concordant among the linkage and temporal methods, ranging from 33 to 121 in group 2, 157 to 212 in group 1 and 240 to 310 in group 3. The NC estimated for group 3 was much higher than the NC estimates for groups 1 and 2. Despite the large difference in NC estimates, the NE estimates were similarly low in all three groups. The NE/NC ratio was, therefore, lowest in group 3 (Table 4). This ratio is affected by family-correlated survival (i.e. how families survive as a unit [82, 83]) and variance in family size at high NC values [83, 84]. In terms of control, this implies that reducing population size alone without eradication would not constitute a permanent solution because NE levels could be maintained, or even increased when NC is reduced because of a decrease in variance of family size and increase in survival of families as units. The robustness of NE in the face of population reduction can be seen in group 1, which has been subjected to intensive control efforts in the past; despite the low NC, NE was relatively high (the NE/NC ratio was as high as 0.121 compared to 0.101 in group 2 and 0.075 in group 3).
Regression of linearized FST against geographic distance revealed significant IBD within groups 2 and 3, as well as females in group 1. Group 1 comprised only three sampling sites and, thus, we only had three data points for the regression. Despite the scarcity of data points, we observed a significant IBD pattern for the less mobile females by removing the better-dispersing male individuals from the model. Dispersal distances (σ) were similar between the 1D and 2D IBD models. These distances were approximately 14–15 km for flies in group 3 and lower in the other two groups, ranging from 2.5 to 4.5 km (Table 4). Based on the 2D estimates, the dispersal surfaces (σ2) within groups 1, 2 and 3 were 6.2, 12.9 and 200.1 km2, respectively. Similarly, migration rates per generation (m) within the three units ranged from 0.01 in group 1 to 0.03 in group 3. Flies in group 3 cover greater distances and disperse over a wider surface area per generation, suggesting that conditions for movement are more favorable in this region, possibly due to environmental factors.
These genetically derived dispersal distances and migration rates are very similar to estimates of dispersal rates for Gff based on mark-release-recapture (MRR) studies, which are about 14.2 km per generation given the movement estimate of 338 m/day . Our genetic estimates are also similar to MRR estimates for other riverine species, such as G. palpalis gambiensis and G. tachinoides[13, 86]. MRR data do not necessarily correlate with genetic data, as was observed for flies from the morsitans group , suggesting that although habitat fragmentation reduces dispersal capacity, it may not impact levels of intraspecific genetic cohesiveness and that its effect is species-dependent. The relatively low dispersal rates in groups 1 and 2, as compared to group 3 and MRR estimates for Gff suggest that the dispersal capacity of flies is reduced in these areas, probably due to habitat loss and control efforts. The reduction in dispersal capacity has had an effect on genetic cohesiveness in the region and led to the differentiation into distinct genetic groups.
Suppression should be followed by eradication in all three groups. While eradication would be harder to implement in group 3 because of the comparatively larger population size, larger dispersal distance and surface per generation, even the best suppression efforts would be much more difficult to maintain over time. Thus, the better option would be for an eradication campaign to follow an initial suppression phase post-haste, much more rapidly in group 3 than the other two groups.
The dispersal of flies across our study area showed evidence of sex bias. While male-biased dispersal in group 3 was only supported by mAIc, evidence for male-biased dispersal was stronger in groups 1 and 2. The finding of male-biased dispersal is very valuable for sterile insect technique (SIT) vector control efforts. The release of sterile male flies, as the better dispersing sex, holds the promise of sterile individuals being able to efficiently compete with wild breeders.
The findings of this study have reaffirmed the importance of gathering genetic data prior to implementing area-wide tsetse vector control operations. The high levels of genetic mixing between islands and mainland sites suggest that these sites should be treated at the same time. The boundaries of the PATTEC blocks need to be modified to reflect the genetic composition of fly populations (i.e., three genetic groups). Fly populations from the two westernmost groups (1 and 2) are relatively isolated from flies in group 3, suggesting that suppression followed by eradication measures can be effective in these regions, but only if area-wide approaches include both island and mainland sites. For group 3, high levels of gene flow, which translate to a large dispersal surface (σ2 = 200 km2), as well as a very large census size and the potential for the NE/NC ratio to increase in the case of population size reduction, all suggest that suppression alone is not likely to produce desirable results in the long run and that it should be coupled with eradication. Additionally, following the initial suppression phase, eradication would have to ensue faster for group 3 than the other two groups in order to overcome the comparatively higher dispersal capacity of flies and prevent re-infestation. The high dispersal rate in group 3 is a strong argument against the Buvuma islands being a suitable location to evaluate eradication protocols, and that the Ssese islands are a better target for this purpose, provided mainland sites are also included. The finding of male-biased dispersal of tsetse populations in this region ensures that eradication efforts involving SIT are likely to be successful.
This study was supported by grants from NIH (R01 AI068932 and D43 TW007391) to SA, AC and LMO, and WHO-TDR (A80132) to AC and LMO. The research was accomplished while ABK was a Fogarty Research Fellow at Yale University. We are thankful for the support of Drs. Vincent Muwanika and Anne M. Akol (Makerere University, Uganda), PATTEC Uganda’s STATFA Project and Mukono District Administration. We are grateful to the technical staff of NaLIRRI for excellent assistance with field sampling.
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