Population structure and invasion history of Aedes aegypti (Diptera: Culicidae) in Southeast Asia and Australasia

Abstract The dengue mosquito, Aedes aegypti (Linnaeus, 1762), is a highly invasive and medically significant vector of dengue, yellow fever, chikungunya and Zika viruses, whose global spread can be attributed to increased globalization in the 15th through 20th century. Records of the invasion history of Ae. aegypti across Southeast Asia are sparse and there is little knowledge regarding the invasion routes that the species exploited to gain a foothold in the Indo‐Pacific. Likewise, a broad and geographically thorough investigation of Ae. aegypti population genetics in the Indo‐Pacific is lacking, despite this region being highly impacted by diseases transmitted by this species. We assess 11 nuclear microsatellites and mitochondrial COI sequences, coupled with widespread sampling through the Indo‐Pacific region to characterise population structure at a broad geographic scale. We also perform a comprehensive literature search to collate documentation of the first known records of Ae. aegypti at various locations in the Indo‐Pacific. We revealed additional spatial population genetic structure of Ae. aegypti in Southeast Asia, the Indo‐Pacific and Australasia compared with previous studies and find differentiation between multiple Queensland and Torres Strait Islands populations. We also detected additional genetic breaks within Australia, Indonesia and Malaysia. Characterising the structure of previously unexplored populations through this region enhances the understanding of the population structure of Ae. aegypti in Australasia and Southeast Asia and may assist predictions of future mosquito movement, informing control strategies as well as assessing the risk of new invasion pathways.

recent changes in human water storage practices and climate has resulted in the evolution of a highly anthropophilic subspecies, Aedes aegypti aegypti, which uses artificial water-holding containers as larval habitat (Brown et al., 2014;Rose et al., 2020). The evolution of anthropophily in Ae. aegypti has dramatically increased its diseasetransmitting potential (Ritchie, 2014), and its use of artificial containers as larval habitat and desiccation-resistant eggs has contributed to its successful invasion of most of the world (Brown et al., 2014).
With a widespread distribution in urbanised areas of the tropics and subtropics, it is a major pest and acts as the principal vector of dengue, chikungunya and Zika viruses (Rose et al., 2020). Although the broadscale global invasion history and population genetics of Ae.
aegypti has been studied extensively, finer scale invasion pathways and population structure in some regions are less well known. In this study, we focus on improving knowledge of population structure and invasion history of Ae. aegypti in Southeast Asia, particularly the Indo-Pacific.
It is likely that Ae. aegypti first established in Asia in the late 19th century, coinciding with the first reports of dengue fever from an urban setting where Ae. aegypti was the suspected vector (Smith, 1956). In Southeast Asia, the first evidence for the establishment of the species is at major ports around the Malaysian Peninsula in Singapore in the early 1900s, Fontaine (1899) quoted by Thoebald (1901), Port Klang (Malaysia) (Daniels, 1908) and Indonesia (Java, Sumatra andSulawesi, 1901-1916) Marlatt quoted by Howard et al. (1917), (Boyce, 1911;Schüffner & Swellengrebel, 1914;Stanton, 1920), before spreading along the coast and then inland.
Other regions of Asia showed mostly coastal distributions or only establishment at major ports, suggesting later introductions in regions including Thailand, Vietnam, India, Myanmar and China (Farner et al., 1946;Kumm, 1931;Theobald, 1911). Ports in the Bay of Bengal could have acted as an important introduction pathway into Asia given its strong history of trade; although the first occurrence records were from 1899 in India; Goodrich (1899) and James (1900) quoted by Theobald (1901) and 1901 in Upper Myanmar (Watson quoted by Theobald, 1901). Recent molecular studies examining the global population genetics of the species have suggested that the 'Asian' (including some populations from the Pacific and Australia) invasion of Ae. aegypti was most likely seeded from the Americas rather than from an African source (Brown et al., 2014;Gloria-Soria et al., 2016;Powell & Tabachnick, 2013). Other such studies present conflicting results and pathways (West Africa to Asia to the Americas; see Bennett et al., 2016), albeit with low confidence in results. However, these studies were performed at a global scale and combined broad geographic regions to simplify invasion scenarios.
In Australia, reports of dengue suggest the species established at a similar time as in the Asian region, possibly prior. The first indigenous outbreaks of dengue in Australia occurred in Townsville, Queensland (QLD) in 1879 and later in Rockhampton, QLD in 1885 (Lumley & Taylor, 1943a), with several epidemics later described during the 1890s and early 20th century (Mackenzie et al., 1996).

Records of urban endemicity of dengue commenced in India and
Indonesia from the late-1800s to early-1900s for mainland Southeast Asia (Smith, 1956), although little interest was paid to dengue during this time. Unlike the recent arrival of Aedes albopictus into northern Australia which appears to have originated from Indonesia (Beebe et al., 2013;Maynard et al., 2017), genetic evidence (SNP and nuclear gene sequences) suggests the older invasion by Ae. aegypti into Australia was likely from an Asian, American or Western Pacific source (Gloria-Soria et al., 2016;Powell & Tabachnick, 2013). The possibility of the Mediterranean acting as an invasion source following the opening of the Suez Canal has also been suggested (Powell et al., 2018).
The first specimen of Ae. aegypti in Australia was recorded from the remote inland Queensland town of Cunnamulla in 1881 (Lumley & Taylor, 1943b;Taylor, 1915a), shortly followed by a record from Brisbane in 1887 (Skuse, 1889). Once in Australia, Ae. aegypti spread rapidly via rail (Hamlyn-Harris, 1927), both inland and along the coast. Since then, its distribution has decreased substantially due to reduction in rainwater tanks in the second half of the 20th century (Beebe et al., 2009;Trewin et al., 2017). Today, it is only found in Queensland, where it is responsible for occasional outbreaks of dengue fever in northern regions. Past studies have shown that the Torres Strait Islands' population of Waiben are mitochondrially distinct from other northern Queensland populations (Beebe et al., 2005).
Records of Ae. aegypti in New Guinea start in 1907 (Theobald, 1907), and more specifically noted in Friedrich Wilhelmshafen (now Madang, Papua New Guinea) and Dorey (now Manokwari, West Papua, Indonesia) later in 1910 (Walker & Biro quoted by Theobald, 1911). Aedes aegypti was also found on steamers, De Rook quoted by Bonne-Wepster and Brug (1932) travelling to Tanah Merah (southern Netherlands New Guinea) and at various locations in the New Guinea region between 1910 and 1930s (Hill, 1925;Howard et al., 1917;Stanton, 1920;Taylor, 1914Taylor, , 1915bTheobald, 1911). Farner et al. (1946) noted the species' distribution was somewhat discontinuous in New Guinea and limited to areas connected through sea and river traffic (Farner et al., 1946); a pattern which was still apparent in 1987 (Lee et al., 1980), reflecting the species' strong ties to human movements.
To the east, in the Nggella Islands of the Solomon Archipelago, Ae. aegypti was common in the houses of Tulagi (the then capital city) Garment quoted by Edwards (1925), Ferguson (1923) and the nearby Purvis Bay in 1925; White quoted by Buxton (1927). This suggests that the species began to establish in the Solomon Islands around the 1920-1930s. Troop movements into the Pacific Islands during World War II are likely to have greatly expanded the distribution of Ae. aegypti and contributed to the dispersal between geographically distant and genetically distinct populations (Calvez et al., 2016;Failloux et al., 2002). For an overview of occurrence records within Southeast Asia and Australasia refer to Figure 1 and Table S1. Overall, the records presented in the figure show that the first recorded appearances of Ae. aegypti occurred rapidly and at a similar timeframe at the turn of the 20th century ( Figure 1). These correspond broadly with urban dengue and chikungunya records in the region (Carey, 1971;Mackenzie et al., 1996;Smith, 1956). By the 1940s, Ae. aegypti was ubiquitous in the tropics of the region (see Farner et al. (1946) distribution map), but remained absent from certain areas Kraemer, Sinka, Duda, Mylne, Shearer, Brady, et al., 2015).
In this study, we aim to first document the invasion history of Ae. aegypti in the Indo-Pacific region from historical literature and secondly further investigate the population structure of Ae. aegypti in the Indo-Pacific region by including previously unstudied populations and geographic areas. We hypothesise that the population structure of Ae. aegypti is characterised by both isolation by distance and historical and contemporary human transportation routes. We expect that the species' invasion into Southeast Asia and Australasia involved a history of multiple, independent introductions and that this will be reflected in our population genetic data.

| Sampling and species identification
Our collection sites consisted of 20 populations distributed throughout the Southeast Asia and Australasia region (Figure 1, black triangles). This included populations from Arizona (USA), Australia, New Guinea (Papua New Guinea and Papua-Indonesia), the Solomon Islands, Indonesia (Bali, Sulawesi and Sumba) and mainland SE Asia (Malaysia, Thailand and Cambodia; Table 1; Table S2). Adult samples were collected between 2008 and 2016 using aspiration/ sweep netting while larvae were collected from suitable breeding habitats using dipping. Samples were either stored in 70%-100% EtOH or desiccated (adults) over silica beads. DNA was extracted from samples of Ae. aegypti using a salt extraction protocol (Beebe et al., 2005) and diluted at 1:10 in 1 × TE buffer (Tris, EDTA). Species identification was verified through morphology or in difficult cases using PCR-restriction digest species diagnostic (Beebe et al., 2007).

| Microsatellite amplification, allele scoring and analysis
Samples were screened for 11 microsatellite markers (Table 2). These markers have been employed in previous population genetic studies on Ae. aegypti (Calvez et al., 2016). We attempted to use an additional microsatellite marker (AG2) but found that this consistently failed to amplify in many samples and was thus excluded early in the study. Microsatellites were amplified and tagged with fluorescent dye using M13 tails in 15.4 μL reactions consisting of 10.8 μL H 2 O, 3 μL 5 X Mytaq buffer (Bioline, with pre-optimised concentrations of dNTPs and MgCl), 0.1 μL 10 μM M13 tagged forward primer, 0.2 μL F I G U R E 1 Sample sites of the present study and invasion history of Aedes aegypti with regards to historical presence records. This figure does not necessarily reflect the actual date of invasion, but provides an overview based on some of the first records of Ae. aegypti in the study region . Circles indicate occurrence records and are colour-coded based on timing (corresponding to the timeline [left]). Black triangles represent sample sites in the present study (refer to Table 1 for population names; Tucson, Arizona population excluded from the figure). The yellow-shaded area represents an early distribution map of Ae. aegypti by Theobald (1911) which has been modified slightly to fit the current map and to correct Australian records from Southern Australia (which were unreliable: see Lee et al., 1980). Dashed dark grey lines show major shipping routes as a result of the opening of the Suez and Panama canals, while lighter grey lines show the density of shipping movements between 1784 and 1863 (US Maury Collection; modified from Ben Schmidt). For plotted records see Table S1.
10 μM reverse primer, 0.2 μL M13 tagged fluorescent dye (VIC, NED, PET or FAM), 0.01 μL (1 U) MyTaq polymerase and 1 μL of 1:10 DNA template. Subsequent PCR involved denaturation at 96°C for 3 min, followed by 13 cycles of denaturation at 95°C for 30 s, annealing at 56°C for 40 s (with a gradient decrease of 0.5°C/cycle) and extension at 72°C for 30 s. This was followed by a further 25 cycles of 95°C for 30 s, 50°C for 40 s and 72°C for 30 s. Then a final elongation step of 5 min at 72°C before cooling to 4°C. Amplification was confirmed by running 1 μL of the PCR product on a 2% agarose gel stained with MidoriGreen (Bulldog Bio; 1 μL per 100 mL of 2% agarose in 1 × TBE buffer). Successfully amplified samples were sent to Macrogen Inc.
(Republic of Korea) for fragment analysis on an ABI 3730XL DNA analyzer (Applied Biosystems, Waltham, Massachusetts, USA).
Raw microsatellite data were processed using the standardization run wizard (default animal fragment settings) in GeneMarker v.2.4.2 (SoftGenetics LLC; Hulce et al., 2011) and alleles were scored manually. A random selection of genotyped plates was scored by a second person to assess consistency in results. Poor-quality samples with weak or messy peaks were removed from the final data set due to an excess of missing data; additionally, those with fewer than eight out of 11 scored loci were removed. This left 366 individuals for the final analyses (Table S2).
Population structure was investigated using the program STRUCTURE v.2.3.4 (Pritchard et al., 2000). Preliminary analyses were conducted to investigate the most probable number of population clusters (K) present in the dataset and to explore the effect of models using the admixture and population prior settings. Based on these preliminary analyses, the final analysis was run with the admixture model and using sampling locations as a prior, with K ranging from 2 to 22 (20 iterations per value of K) with a burn-in of 100,000 followed by 1,000,000 iterations. The output from the STRUCTURE run was processed in STRUC TUR EHA RVE STER (Earl & vonHoldt, 2012) to infer the most likely value of K using the Evanno ∆K (Evanno et al., 2005) and L(K) methods. In addition, we analysed subsets of the dataset based on these STRUCTURE results (commonly referred to as a hierarchical approach, where distinct clusters are sub analysed in independent STRUCTURE runs to explore any substructure). For these sub-analyses, we used the same settings and run time, but the value of K ranged based on the number of populations being analysed. Final plots were made using pophelper (Francis, 2017). CLUMPAK (Kopelman et al., 2015) was used to assess K values for each analysis.
We conducted discriminant analyses of principal components as an alternative approach to examine population structure in our dataset using adegenet. Due to the highly domestic nature of Ae.
aegypti (Powell & Tabachnick, 2013), group membership was predefined based on sampling location (Table 1; Population) and DAPC was initially conducted on the whole dataset. We performed crossvalidation on the DAPC using a validation set of 10% and a training dataset of 90% with 100 replicates. To avoid overfitting the discriminant functions in DAPC, we considered the optimum number of principal components (n.pca = 30) to retain as that being associated with the lowest root mean squared error (RMSE; Jombart & Collins, 2015). Five discriminant functions were retained but only the first three were plotted as these explain the most variance. To assist with the display of results, we additionally plotted population means from the DAPC to highlight patterns and reduce noise in the plots.
To further explore clustering in our dataset given no prior population information (i.e. assuming populations are unknown), we used K-means clustering where the various clustering outcomes were compared using the Bayesian information criterion (BIC).
The K-means clustering was performed using the adegenet package (using PCA where all principal components were retained). We used the lowest BIC to infer the optimal K value. Inferred group memberships were plotted against actual group (population) membership. We additionally performed this using regional definitions (Table 1; Region) to explore how this affected reassignment of individuals.

| Mitochondrial COI amplification and analysis
An approximately 550 bp region of the mitochondrial gene COI was amplified using previously used (Beebe et al., 2005) primers quencing. An automated workflow was used in Geneious v.11.1 (http://www.genei ous.com, Kearse et al., 2012) to first trim ends of the sequences (error rate 0.01%), de novo assemble forward and reverse sequences from the same individuals (at which point alignment and chromatogram quality was visually assessed for all sequences) before extracting a consensus sequence for each individual. Sequences that were not processed in the workflow due to either/both forward/reverse reads being low quality were visually inspected; if one read was of acceptable quality (≥65%) then this single read was used to generate a sequence. From the 117 individuals sequenced, 111 sequences were of adequate quality.
Additional COI sequences of Ae. aegypti were obtained from Genbank (810 sequences total, 111 produced in this study, Table S3). Sequences were aligned in Geneious using the MAFFT alignment (Katoh & Standley, 2013). All sequences were trimmed to 335 bp to incorporate the large number of COI sequences from Genbank, many of which were smaller than, or did not overlap fully with, the ~550 bp region sequenced in this study. Sequences were checked for stop codons and a TCS haplotype network was constructed in PopArt v.1.7 (http://popart.otago.ac.nz) using 1000 iterations.

| Genetic diversity and differentiation (F ST , Jost's D and G" ST )
We  Note: Regional and population definitions are shown, as are population abbreviations used in some figures and text. Sample size (n) is also indicated per population. Regional abbreviations that are used in approximate Bayesian computation are shown in brackets in the 'Region' column. Further details are in Table S2.  (Table S5). Overall, the mantel test showed a significant relationship between geographic distance and genetic distance (y = 0.0001x + 5.2284; p = 0.0002), but the correlation is weak (R 2 = 0.009), implying the influence of other factors shaping the genetic structure of Ae. aegypti in the study region.
There was no major difference in the relationships observed using multiple measures of genetic distance (Table S5;

| Population structure-microsatellites
Aedes aegypti shows a clear spatial genetic structure in our study region. Using STRUCTURE (Figure 3), populations were more clearly differentiated without the admixture model and using sampling locations as a prior, which assists with clustering when population structure is somewhat weak (Pritchard et al., 2009). However, here we present and discuss results using the admixture model and location prior settings as it provides a more realistic depiction of the population processes occurring within this highly anthropophilic species, which has likely experienced on-going human-mediated dispersal and hence admixture between populations.
For the whole dataset, ∆K suggested two genetic clusters in the study region (Figure 3). At K = 2, the clusters generally correspond to an Australian (red) and Indonesian/Malaysian ( were analysed together, the optimal K-value ranged from 4 to 7.
When K = 4, genetic clusters correspond to broad geographic groupings: Torres Strait, Papua New Guinea/Solomon Islands, Southeast Asia and the USA.
Discriminant analysis of principal components of the full dataset ( Figure 4) Figure S4). When the data were analysed using DAPC with broader regional definitions rather than using population information, individuals were mostly assigned to their original cluster with a few exceptions. The proportion of correct reassignment to the original population was 0.41 when populations were used compared to 0.85 when broad regions were used ( Figure S5).

| Population structure-Mitochondrial COI
Using the mitochondrial marker COI did not reveal a strong genetic structure, but some patterns regarding the distribution and diversity of haplotypes are worth noting. The 13 haplotypes plotted in

| Population structure
The population structure of Ae. aegypti across our entire study region are consistent with those of global studies (Gloria-Soria et al., 2016), and others that share overlap with our study region . Consistent with these studies, we find that Australian populations belong to a genetic cluster distinct from Asian and Indonesian populations. This study revealed additional spatial population genetic structure of Ae. aegypti in Southeast Asia and Australasia compared with previous studies, particularly when populations were analysed using a hierarchical approach.
Notably, within Australia, we found differentiation between multiple Queensland populations as well as between the northern Australian Waiben (Thursday Island, Torres Strait Islands) populations. When We found a significant positive relationship between geographic and genetic distance that hints at a subtle pattern of isolation by distance, supporting the results of other studies (Endersby et al., 2009;Schmidt et al., 2020). However, the correlation (R 2 ) was weak, implying that other drivers such as human movements play an important role in shaping the genetic structure of Ae. aegypti in Queensland.
In a previous study, Endersby et al. (2009) (Crawford et al., 2017;Fonzi et al., 2015;Gonçalves da Silva et al., 2012;Huber et al., 2004;Powell et al., 2018;Rasheed et al., 2013;Schmidt et al., 2020). know about the biology of Ae. aegypti, it is likely that there is real population genetic structure between these sites, but that relatively small sample sizes reduced our ability to detect significant F ST between these sites. Low genetic differentiation between these sites may be due to either gene flow or a recent shared ancestry between them.
The positive relationship between genetic distance and geographic distance is also obvious in the Waiben population from the Torres Strait Islands, which is the most disconnected Australian The globally widespread COI haplotype H14 was prevalent on Waiben but was not detected in mainland Australia. This is probably reflective of the Torres Strait region differing in invasion and demographic history from mainland Australia, reinforcing earlier findings by Beebe et al. (2005). The Torres Strait Islands have a higher incidence of dengue compared to mainland Australian populations.
Additionally, Ae. aegypti from Waiben are more competent vectors F I G U R E 5 Thirteen of the most prevalent COI haplotypes for Aedes aegypti on a global scale. Circle size corresponds to the number of sequences (see white dashed scale) from a given locality. The proportion of individuals belonging to a given haplotype is colour-coded in the key (right). Refer to Table S3 for specific details and location numbers.
of dengue serotypes 2 and 4 compared to those from Cairns and Townsville (Knox et al., 2003), highlighting the connection between genetic structure and medically relevant traits such as vector competency. From a historical perspective, the Torres Strait Islands were part of an extensive pearling industry during the 1880s, which sought a workforce primarily from the Pacific Islands (chiefly Fiji, Vanuatu and New Caledonia), Japan, Malaya and the Philippines (Beckett, 1977). In the Pacific Islands, the Honiara (Solomon Islands) population appeared more genetically distinct from the nearby population of Port Moresby than expected and is somewhat unique within our study area. This is potentially due to mixed ancestry  (Calvez et al., 2016;Failloux et al., 2002;Powell et al., 2018). One of the most comprehensive genetic studies on Ae. aegypti in the Pacific (including multiple islands from New Caledonia, Fiji, Tonga and French Polynesia, but not the Solomon Islands) found moderate genetic differentiation between island populations (F ST = 0.05-0.24) and that populations from more isolated islands were more genetically distinct than those from major towns, which showed a higher degree of mixed ancestry (Calvez et al., 2016). Nevertheless, their microsatellite data revealed population differentiation in the Pacific region, broadly corresponding with western, central and eastern genetic divisions, with further substructure within these divisions. The mtDNA markers (COI and ND4) used in their study revealed some geographic patterns of relatedness between populations, but certain haplotypes were more widespread than others. Their study highlighted that different regions likely had multiple introduction origins, both historic and contemporary. We suspect that populations from the Solomon Islands probably share some similarities to populations from other Pacific Islands ( Additionally, they showed evidence of strong genetic differentiation between French Polynesian populations, which was more obvious than that between populations from Vietnam, Cambodia and French Guiana. This may have been the result of past major bottlenecks (Failloux et al., 2002) but could equally be suggestive of varying invasive origins for the isolated islands in the Pacific.  Figure 1 and records in Table S1). James (1913) points out early concerns that the opening of the Suez Canal (in 1869) and Panama Canal (in 1914) would increase the spread of Ae.

| Invasion history in Australasia and Southeast Asia
aegypti and associated diseases, and this were reiterated recently by Powell et al. (2018). Indeed, the opening of both canals dramatically shaped trade routes, resulting in more direct passages between Asia/Australia with the Mediterranean and the Americas. The timing of the opening of the Suez Canal in 1869 and the emergence of the first urban outbreaks of chikungunya (Carey, 1971) and dengue (Smith, 1956) shortly after support the hypothesis that this acceler-  (Crawford et al., 2017). Future studies using genome-wide SNPs will provide significant insights into the evolutionary and invasion history of Ae. aegypti.

| Limitations, future work and conclusions
One of the main limitations of this study is the relatively small sample sizes for some sampling sites. This may affect estimates of allele frequency and diversity (Hale et al., 2012), as well as potentially reducing power to detect population structure. Another potential limitation of this study is the use of sampling sites as priors for DAPC analysis rather than informing priors from STRUCTURE analyses.
Sampling sites were used as priors in DAPCs due to low assignment probability of many individuals in STRUCTURE analyses, suggesting admixture or shared ancestry, making it difficult to definitively assign some individuals to populations based on STRUCTURE results.
Additionally, using a hierarchical approach in STRUCTURE analyses has the advantage of detecting finer scale structures that may not be apparent when analysing the entire dataset. However, it is important to be aware that once the data are separated into subsets, it will not be possible to see evidence of admixture/shared ancestry between broader groups/populations.
Microsatellites provide relatively few markers compared to what can be achieved with genome-wide SNPs which also needs to be considered in drawing conclusions. Nonetheless, Rašić et al. (2014) (Rašić et al., 2014). We expect that future studies employing genome-wide SNPs with more comprehensive geographical sampling in the Asia-Pacific will reveal finer scale population genetic structure and reveal more details regarding demographic histories in the region. This high level of spatial structure has been shown recently by Schmidt et al. (2019) using genome-wide SNPs in Ae. aegypti from various global populations. Whether populations display seasonal differentiation in genetic structure should also be tested with such markers, however, others have found stability across the wet-dry seasons in northern Queensland (Endersby et al., 2011) and Indonesia (Rašić et al., 2015), which might be the result of eggs surviving the dry season and hatching at the start of the wet season. As seasons are more pronounced at southerly latitudes it would be reasonable to predict that more southerly populations could undergo greater temporal genetic changes. Future genome-wide datasets will likely uncover clearer spatial divisions within populations of Ae. aegypti within Australia (for instance, using landscape genomic approaches; Schmidt et al., 2019Schmidt et al., , 2020 and potentially temporal structure in regions. Importantly, our study demonstrates the need to analyse populations of Ae. aegypti in the Asia-Pacific region at a finer scale to better uncover inter-and intra-continental population dynamics. This has direct implications for identifying invasion pathways for biosecurity (Endersby-Harshman et al., 2020;Schmidt et al., 2019Schmidt et al., , 2020 and for understanding the evolutionary processes that might influence the epidemiology of Ae. aegypti-borne diseases. The genetic differentiation observed between regional towns in Queensland (Australia) suggests that population removal may be possible using the incompatible insect technique. This has recently been shown to be an effective tool for suppressing Ae. aegypti populations in north Queensland towns (Beebe et al., 2021). This type of knowledge regarding fine-scale population structure could be applied to other invasive insects, enabling more specific and informed decisions to be made in control management. Ultimately this would result in improved economic and public health outcomes.

ACK N O WLE D G E M ENTS
The research was supported by the CSIRO Cluster Collaboration Fund 'Urbanism, Climate Change and Health' and the 'Funding Initiatives for mosquito management in Western Australia' (FIMMWA). We thank Alicia Perkins for providing the Tucson (USA) field-collected adult females of Ae. aegypti. Thank you to James Hereward, James Wisdom and Maddie James for providing feedback on drafts.

CO N FLI C T O F I NTE R E S T S TATE M E NT
Authors have no conflict of interest.