Invasive alien species pose a threat to biodiversity, ecosystems, agriculture, human and animal health, and consequently inflict economic damage (Pyšek & Richardson, 2010). Invasive weeds smother and crowd out indigenous flora, thereby threatening local fauna; some release allergenic pollens harmful to many humans, while invasive waterweeds clog and choke natural waterways. The introduction of an alien flora species may concurrently introduce alien parasites, fungi, invertebrate larvae or diapausing eggs, hosted by that species in its environmental niche. Such hosted species may be potential vectors of novel pathogens into their new environment. Similarly, some invasive alien insect species may be vectors of diseases of epidemic potential (Antia et al., 2003) that can be medically, socially and economically devastating (Pimentel, 2011). Despite the advanced control mechanisms of modern public health, and stringent standards imposed at borders to control what travelers and traders carry in and out through border posts, invasive alien species still penetrate and establish an environmental presence. Whether or not the potential health and economic impacts of such invasions have been quantified, logic demands the elimination of such potentially dangerous invasive alien species as a precaution, as quickly as possible (Wittenberg & Cock, 2001). In practice, aside from invasions of pests that have an economic impact and act as vectors of disease, response is often delayed (Hulme, 2006).
Aedes albopictus, or the Asian tiger mosquito, a belligerent insect that bites during the day, has emerged as a threat to public health worldwide and has been identified as the vector of the Chikungunya and Dengue viruses, among others. Most recently it has been verified in Brazil that Ae. albopictus is a potential vector of Zika virus, of which its closest relative, Ae. Aegypti, has been the major vector thus far (Schaffner, Medlock & Bortel, 2013). Ae. albopictus is one of the world’s one hundred worst invasive species according to the Global Invasive Species Database (GISD, 2017). This devastating impact has been facilitated by a rapid spread from its native East Asian to western Pacific and Indian Ocean natural domains (Caminade et al., 2012).
While the species has had multiple introductions to Australia and New Zealand, it has not established itself there, mainly attributable to the efficiency of entomological surveillance in the airports and harbors of these countries (Ritchie et al., 2006).
Ae. albopictus was established in the USA in 1980, ostensibly arriving in a shipload of used tires from Japan. (Rai, 1991). Once Ae. albopictus establishes in a particular locality, eradication becomes virtually impossible, and costly vigilance and control becomes essential (Holder et al., 2010).
The observed suitable climate for Ae. albopictus growth now ranges from temperate through sub-tropical to tropical, with vegetation from savanna to evergreen and Amazon forest. It can adapt to both arid and humid conditions (Kraemer et al., 2015a; Messina et al., 2016; Vega-Rúa et al., 2014). Winter temperatures appear to be a limiting factor of further spreading of the species (Hanson & Craig, 1994; Rochlin et al., 2013a; Thomas et al., 2012), while winter precipitation may moderate the suitability of the species to colder temperatures (Hanson & Craig, 1995). The natural Ae. albopictus habitat was originally forest edges where they bred in tree holes, stumps of bamboo and bromeliads. Thus, the species was formerly classified as a specifically rural vector (Higa, 2011). However, Ae. albopictus has demonstrated an exceptional ability to adapt to new environmental conditions and establish itself. In urban and suburban environments, it may be found breeding in manmade containers such as external water tanks, animal water troughs, bird baths, plant containers, moist organic matter and abandoned tires, in both towns and suburbs (Caputo et al., 2012). The species is now considered the major vector, and in certain areas the sole vector, of such environments (Caputo et al., 2012). Invasive alien mosquitos often displace the indigenous mosquito territorially. However, the only known case of an invasive alien replacing another invasive alien mosquito species is the displacement of Ae. Aegypti by Ae. albopictus (Kenis et al., 2009), which has been researched and corroborated in Florida, USA. Ae. Aegypti is the major international vector of Zika, and Ae. albopictus has been recently acknowledged as a potential vector, which will certainly have an impact on an outbreak of Zika in any region of such displacement (Ding et al., 2018; Kenis et al., 2009; Nihei et al., 2014; Simard et al., 2005; Weaver & Lecuit, 2015). It should be mentioned that Ding et al. (2018) have recently mapped the spatial distribution of Aedes aegypti and Aedes albopictus for the current time through temperature suitability, NDVI, precipitation, urban accessibility, night time light, urban regions, relative humidity, and population density.
USA public health departments in both rural and urban communities, which previously had no need for developing strategies to control mosquitos, now face the challenge of Ae. albopictus (Rochlin et al., 2013a), which poses a threat to the region without the development of novel methods of control. Existing mosquito controls generally have involved aerial spraying of easily accessible marshland and floodwater breeding grounds. However, the Ae. albopictus partiality for smaller scale, protected breeding in close range of humans in water storage and other moist semi-enclosed artifacts, evade existing control methods. The alternative means the necessity for communities falling within the paths of expansion to deal with the impact. The involvement of a complete community is vital. The crucial issue is whether new strategies can be developed at a relatively low cost. Projecting regions of expansion and general forward planning and sufficient funding through greater public awareness will be the key to effective campaigns. In terms of Ae. albopictus adaptation from rural to urban surrounds, and the need for policy makers and public health organizations to prioritize resources, crucial decisions will need to be made on whether to focus generally on regions with suitable climate, or rather on specific non-climatic parameters such as roads, lakes, rivers, altitude and slope within climatically suitable regions?
The answer to this question is synonymous with the aim of this study which sets out to determine whether Ae. albopictus distribution is more associated with non-climatic parameters or climate suitability?
The current distribution of Ae. albopictus in the southeastern region of the USA was used to develop two separate models for this species of mosquito, based on (i) regions with suitable non-climatic factors, and (ii) regions with suitable climate. The non-climatic model comprised a data-driven Evidential Belief Function with six conditioning factors: (i) altitude, (ii) slope, (iii) aspect, (iv) distance of locality from road, (v) distance of locality from river and (vi) geology, through ArcGIS. The climatic model was based on two GCMs of Miroc3.2 and CSIRO-MK30 for the current time under RCP 8.5 scenario and employed MaxEnt software. We hold the view that the methodology and results of this study will promote active surveillance of Ae. albopictus, as well as other invasive insect species. The results of this study will emphasize the need for increasing awareness to promote vigilance and effective control and eradication mechanisms, complementing the current online information networks of the relevant government and non-government bodies.
Study area selection
The study site is located between 75°30′00″W and 92°00′00″W, and 25°00′00″N and 36°30′00″N in USA (Fig. 1). In selecting the study site, we looked for an area exhibiting variations of each conditioning factor, as well as Ae. albopictus presence. For example, in terms of altitude, the study area should display a range of altitudes. Our selected study area had an altitude range from 0 m to 2,031 m above sea level. For geology, the study area had 80 different geological fractures.
In the study, 70% of the Ae. albopictus presence layer, an inventory factor obtained from Global Biodiversity Information Facility database (Global Biodiversity Information Facility, 2017) and Kraemer et al. (2015b), were used for model training while the remainder 30% was reserved for model validation (Fig. 1). The training and testing points cover all the study area and the testing points were selected randomly.
The six geographical conditioning factors (i) altitude, (ii) slope, (iii) aspect, (iv) distance of locality from road, (v) distance of locality from river and (vi) geology, with a grid cell size 90 × 90 m were used to run the EBF model. The quantile classification scheme was used for all conditioning factors, as recommended by Tehrany, Pradhan & Jebur (2013). Altitude, slope and aspect layers were generated from DEM data obtained from EarthExplorer (2014) as shown in Figs. 2A–2C respectively. Distances from road and river layers were generated by Euclidean Distance tool and divided into ten classes using the quantile method, as shown in Figs. 2D and 2E respectively. The geology layer, obtained from the United States Department of Agriculture (USDA) (United States Department of Agriculture, 2017) contained 80 different types of lithology as shown in Fig. 3. The elevation layer was included as it depicts climate variations and the physical barriers limiting dispersion. The road, river and geological layers were included as the greatest densities of Ae. albopictus occur in urban environments (Rochlin et al., 2013a).
Evidential Belief Function (EBF), which is also called Dempster-Shafer theory of evidence, was developed by Dempster (Dempster, 1967), based on the Bayesian theory of subjective probability. Its advantages are the relative flexibility with which it accepts uncertainty and its ability to aggregate beliefs from many sources of evidence (Thiam, 2005). Rather than estimating the validity of probabilities, the Dempster-Shafer technique calculates the nearness of the evidence in proving the validity of a hypothesis (Pearl, 1990). Applications of EBF have been effective in many fields of research that utilize GIS data (Malpica, Alonso & Sanz, 2007).
To produce a hazard index of presence of Ae. albopictus, the conditioning factors were expressed individually as acquired weights and then aggregated (Eq. (1)).
Assuming a set of Ae. albopictus presence conditioning factors C = (Ci, i = 1, 2, 3, …, n), consisting of mutually exclusive and exhaustive factors Ci. C represents the frame of discernment, and a fundamental probability assignment is represented by the function m:P(C) → [0, 1].
The set P(C) includes all subsets of C, as well as C itself and the empty set. m:P(C) → [0, 1] is described as a mass function and satisfies m(Φ) = 0 and ∑ACm(A) = 1, in which Φ represents the empty set and A represents any subset of C. The m(A) estimates to what degree the evidence supports A, which is denoted by Bel (A), a belief function.
There are four basic evidential belief functions attributable to a proposition, based on evidence. These four functions establish the degree of: (i) Belief (Bel), (ii) Disbelief (Dis), (iii) Uncertainty (Unc) and (iv) Plausibility (Pls). Bel represents the lower bound and Pls represents the upper bound of probability (Althuwaynee, Pradhan & Lee, 2012; Awasthi & Chauhan, 2011). Unc is established by the difference between Bel and Pls, and represents the ignorance. Dis represents the degree of probability that the proposition is false.
Dis = 1 − Pls or 1 − Unc − Bel, such that Bel + Unc + Dis = 1. For a case of Cij zero presence of Ae. albopictus, implying that Bel = 0, Dis is reset to zero, whether that is the case or not (Carranza, Hale & Faassen, 2008). EBF can be estimated on the basis of a subjective judgment or calculated on the input of data (Srivastava, Mock & Gao, 2011). By superimposing the inventory map (L) of Ae. albopictus onto the six individual conditioning factor maps, we ascertained the number of pixels with Ae. albopictus presence and absence, for each separate conditioning factor. Assuming that N(L) represents the total of presence pixels and N(C) the total pixels comprising the study site, Cij represents the jth class attribute of Ae. albopictus presence conditioning factors Ci ( i = 1, 2, …, n), N(Cij) is the total of pixels for class Cij, and N(L∩Cij) is the Ae. albopictus presence pixels in Cij. According to (Carranza & Hale, 2003), estimation of EBFs based on data is represented by: (1) (2) (3) where, (4) In Eq. (2) the numerator represents the proportion of Ae. albopictus presence pixels occurring in factor class Cij, while the denominator represents the proportion of Ae. albopictus absence pixels in factor class Cij. In Eq. (4) the numerator represents the proportion of Ae. albopictus absence pixels in factor class Cij, while the denominator represents the proportion of Ae. albopictus absence pixels in attributes excluding factor class Cij. The parameter WCij (Ae. albopictus presence) represents the weight of Cij supporting the belief that Ae. albopictus presence exceeds Ae. albopictus absence. Parameter WCij (Ae. albopictus absence) is the weight of Cij that supports the belief that Ae. albopictus absence exceeds presence.
After calculation of the EBF function for all Ae. albopictus presence conditioning factors, Dempster’s combination rule was introduced to produce the four integrated EBFs (Dempster, 1967). The formulae for combination of two Ae. albopictus presence conditioning factors C1 and C2 are as follows (Carranza, Woldai & Chikambwe, 2005): (5) (6) (7)
Integrated EBFs of the Ae. albopictus presence conditioning factors are applied in sequence by means of Eqs. (5)–(7). Table 1 shows the estimated EBFs for the six Ae. albopictus presence conditioning factors.
|Layer||Classes||Pixels in class||Belief||Disbelief||uncertainty||plausibility|
|Distance of locality from Road (m)||0–252.46||9093909||22||9||69||91|
|Distance of locality from River (m)||0–9,601.28||9750778||11||9||80||91|
|clay or mud||17275519||5||1||94||99|
|ultramafic intrusive rock||13,298||0||1||99||99|
|felsic metavolcanic rock||928277||0||1||99||99|
|mafic metavolcanic rock||138759||0||1||99||99|
|lake or marine deposit (non-glacial)||1159949||0||1||99||99|
|intermediate metavolcanic rock||46,641||0||1||99||99|
|felsic volcanic rock||38||0||1||99||99|
Climatic data, future scenarios and climate models
Baseline climate was represented by the WorldClim current climate dataset of BIOCLIM variables (http://www.worldclim.org). WorldClim is a high-resolution climate average for the period 1961 to 1990, with global coverage and spanning the time period over which the majority of occurrence records were collected. Possible future climates at global scale incorporated four IPCC5 greenhouse gas concentration (GHC) trajectories, which differ in terms of GHC emission peaks. The lower the number of the trajectory, the earlier in the century it peaks.
We purposefully chose the worst (extreme) RCP8.5 (peak 2080) (Stocker et al., 2013) for incorporation into the future climate scenario in the model projections as it is not yet possible to determine which estimates of the climate change and RCPs of 2.6, 4.5, 6.0 and 8.5 are the most reliable (Randall et al., 2007). RCP8.5 is a representative concentration pathway that includes relatively high emissions of greenhouse gases. Other factors assumed in RCP8.5 are high demographic development, relatively slow economic growth, with modest progress in technology and the introduction of novel sources of energy. These factors culminate in an increased demand for energy and higher GHG emissions over the long term, without a more radical approach to the projected impact of climate change (Riahi et al., 2011).
There are 19 General Circulation Models (GCMs) in WorldClim database and we have selected GCMs of Miroc3.2 and CSIRO-MK30, which have higher reputations and have been used for projections of many invasive species, agricultural crops and pests (Da Silva et al., 2017a; Da Silva et al., 2017b; Lamsal et al., 2017; Paterson et al., 2017; Ramirez-Cabral, Kumar & Shabani, 2017b; Ramirez-Cabral, Kumar & Shabani, 2017a; Shabani, Kumar & Ahmadi, 2016; Shabani, Kumar & Ahmadi, 2017; Shabani, Kumar & Taylor, 2012).
MaxEnt desktop version 3.3.3k, with modified parameters, was used to construct the climatic model (Phillips, Anderson & Schapire, 2006; Phillips & Dudík, 2008). MaxEnt requires a user-defined background of geographical data (Guillera-Arroita, Lahoz-Monfort & Elith, 2014) in order to compare the climate of a set of grid cells representing the presence of a species, with the reference set representing the climate of the sampled cells. The selected geopgraphical data is a significant determinant of the results of the model (Elith et al., 2011) and it is important that it reflect all environmental variations covering the areas representing the presence of the species (Elith, Kearney & Phillips, 2010). The algorithm in MaxEnt estimates the maximum entropy probability distribution that approximates uniformity, based on a comparison of presence and background location interactions with a set of variables, limited by parameters imposed by the observed spatial distributions and environmental factors. Optimisation of the maximum entropy probability distribution is achieved by minimisation of the relative entropy between presence and background point data (Phillips, Anderson & Schapire, 2006). MaxEnt, with inbuilt MESS analysis tool, has the capacity to predict future distributions, generated from two datasets of environmental variables (Elith et al., 2011). In our study, the current conditions are used to generate the model, with a set of variables utilized for projection of the future scenario (in this case 2055).
Using jackknife analysis and Pearson correlation technique to correlate coefficients, we selected the most influential variables showing low correlation (R2 < 0.5) for this modeling study. Here, BIO11 (Mean Temperature of Coldest Quarter), BIO16 (Precipitation of Wettest Quarter) and BIO17 (Precipitation of Driest Quarter) were selected for the modeling. To achieve greater consistency of background data and overcome the potential for finding fewer records representing areas more recently experiencing invasions, as well as those incompletely sampled, we assigned greater prominence to the records representing less geographical proximity. However, it should be noted that without information on actual survey returns, there is no method of separating unsuitable and under-sampled areas, and that the weighting of prominence cannot overcome the fusion of these two categories of data. After using the Gaussian kernel method to establish deviations from the ArcGIS default values, the formula applied for weighting is to divide total weighted records by the weighted number of land cells of the specific area, to exclude coastal region edge effects. By adjusting the resulting grid to a range of 1–20, extreme values were excluded. This weighting method, as advocated by Elith, Kearney & Phillips (2010), reduces bias that gives prominence to the records of more densely sampled areas. Background training points were generated from the kernel density layer for the species using Hawths Tools extension (Beyer, 2004).
The non-climatic modeling analysis was executed and validated using known Ae. albopictus presence (Fig. 1). Using training and testing Ae. albopictus presence data, validation was carried out using the area under curve (AUC) method. While training presence data was used to generate the model, the results using this data does not fully represent the model’s total efficiency. The prediction rate was measured to establish how efficiently the model and selected conditioning factors predicted Ae. albopictus presence. AUC can assess prediction accuracy qualitatively by arrangement of the calculated values of all cells of the study locations into descending order, providing an individual hierarchical ranking of the accuracy of each prediction. Thereafter, the values of cells were divided into 100 classes with accumulation intervals of 1%.
We examined, and assessed individually, six geological variable factors that directly impact the presence of Ae. albopictus in a specific locality. The altitude EBFs indicated that localities of 0 to 97 m above sea level had a high probability presence of Ae. albopictus. The belief value (Bel) peaked at 24 with altitudes from 15 to 27 m, while it was 5 and 0 at altitudes from 127 to 167 m and 167 to 228 m respectively (Table 1). Slope EBF indicated that classes of 2.72 to 7.84°, 10.56 to 13.86°and 33.76 to 76.85°produced Bel values of 12, 14 and 4, respectively. The three highest Aspect Bel values of 15, 13 and 12 related to the classes of South, Northwest and Southwest, respectively (Table 1). Distance from locality to road was included as a conditioning factor, as motor vehicles have been shown as a means of Ae. albopictus transmission. The highest Bel values for this factor were 22 and 19, representing the classes of 0 to 252 m and 252 to 757 m, respectively. For Distance of locality from river, EBF estimated the probability of Ae. albopictus presence, for all ten classes (Table 1). For Geology, the classes of unconsolidated deposit, calcarenite and delta scored Bel values of 16 and 14 and 41, indicating the probability of Ae. albopictus presence in these geological formations (Table 1).
Probability index and suitability map
The verification results for EBF model are shown in Fig. 4. Probability index maps of Ae. albopictus presence produced by EBF method are shown in Figs. 5A and 5B respectively. The range is from 0 to 1, where 0 represents zero probability and 1 represents 100% probability. For producing suitability maps, as well as improving the visual interpretation of locational suitability, probability maps require some form of classification (Umar et al., 2014). There are a variety of classification techniques such as equal interval, natural break, standard deviation and quantile, the selection of which should be based on the research data characteristics and study objectives. Equal interval is suitable when the data displays a normal distribution, while standard deviation arranges the data into a fixed number of classes. Natural break suits a dataset exhibiting a sudden or big jump. Here, in order to have a reliable judgment regarding the impact of every class of each factor on species occurrence, we attempted to reduce the influence of classification algorithm on the conditioning factors classes as much as possible. In some population analysis projects where the goal is to find a big jump in the data, natural break technique is highly recommended (Hui et al., 2010; Umar et al., 2014), while in this research, this method would not be efficient. Hence, quantile-based classification technique was found to be more appropriate to classify the factors in this study. This method groups equal number of pixels (area) into each group without any interference in the separation of the pixels. We thus selected the quantile method to produce the suitability classes. The verification results for EBF model are shown in Fig. 4. The AUC results showed 0.73 success rate and 0.70 prediction rate (Fig. 4) and these values are high enough and satisfactory for model prediction as documented in Umar et al. (2014). Our probability indexes were into five zones of suitability: very low, low, moderate, high, and very high, for EBF output (Fig. 5B).
The climatic model produced by MaxEnt, using two GCMs, Miroc3.2 (Fig. 6A) and CSIRO-MK30 (Fig. 6B), under the RCP 8.5 scenario, shows virtually the whole study site is highly suitable for Ae. albopictus and that this condition will persist until at least 2055. Comparing the GCM projections for 2055, CSIRO-MK30 produced a more moderate pattern of climatic suitability than Miroc3.2. Both GCM response curves show the highest probabilities of Ae. albopictus presence in areas with Coldest Quarter Mean Temp (bio11) from 16 to 23 °C, Wettest Quarter Precipitation (bio16) of 430 mm and Driest Quarter Precipitation (bio17) of 350 to 450 mm (Figs. 6A and 6B). The Miroc3.2 mean AUC was 0.868, while CSIRO-MK30 indicated 0.864.
This study undertook a comparative assessment of the proficiency of the EBF and MaxEnt statistical methods in mapping the probability of Ae. albopictus expansion based on climatic and non-climatic parameters respectively. Based on AUC validation method, both EBF and MaxEnt had high prediction rates and thus both can be used to generate Ae. albopictus expansion probability and suitability for current and future time. Such maps would assist national, regional and local public health organizations in the identification of areas, and their degree of suitability to Ae. albopictus expansion or invasion, as a blueprint on which to plan and implement prevention or reduction measures, or to prepare for potential invasion. Suitability maps provide a foundation for more refined analytical tools such as hazard and risk mapping. It is important to note that the accuracy of Ae. albopictus expansion risk is dependent on the accuracy with which the conditioning factor values are calculated. Beyond the establishment of the class, it is essential to understand which conditioning factors impact most on Ae. albopictus expansion or invasion. Once the conditioning factors and associated severity of impact have been established, the information is valuable as a foundation to conservation strategies to protect areas at risk.
We also highlight that through the Miroc 3.2 model, the overall suitability remains the same by 2055, while the suitability will slightly decrease by 2055 in the CSIRO-MK30 model and the possible explanation of this difference is due to each GCM and SDM functioning slightly differently and, in line with this matter, Shabani, Kumar & Ahmadi (2017) has recently documented that comparison of the individual SDM or GCM to an ensemble approach showed that there was a better agreement between the ensemble outputs under different GCMs or SDMs. This finding is in line with Araújo & New (2007), who have recommended that using ensemble forecasting has clear advantages over single model forecasts.
Our results indicate the importance of both climate and non-climate factors on the degree of potential Ae. albopictus expansion. Complementary to this finding, a number of studies have shown the inability of diapausing Ae. albopictus eggs to survive extreme winter temperatures (Hanson & Craig, 1994). Urban habitats with high levels of organic material, such as sewerage treatment works and storm water drainage systems, can impact on the extent of Ae. albopictus expansion and such larval habitats should be treated with well-developed methods providing long term relief for the entire Ae albopictus season (Rochlin et al., 2013b). Our results also indicate that in terms of climatic suitability, and predicted future climate scenarios, this study has validity and will remain valid in the future for Ae. albopictus (Fig. 6), particularly for the USA. Almost one-third of the study site was identified as being at high risk of Ae. albopictus expansion, based on the location of suitable non-climatic parameters alone (Fig. 5). Our results show the importance of non-climatic parameters in that these can be used to further refine high probability areas within climatically suitable regions. Thus, in terms of offering Ae. albopictus control services, the climatic result is not as useful on a practical basis as the non-climatic result due to the overall climate suitability of the whole study site. However, the projected future impact of non-climatic parameters on Ae. albopictus expansion for the future was not undertaken as the road and river layers will change.
The EBF outputs for altitude conditioning factor indicated that areas from 0 to 97m above sea level had a high probability of Ae. albopictus presence, which may be attributable to the greater instability of organic material, water or other non-climatic factors at higher elevations. Moisture preservation and distribution of vegetation amount are related to slope and aspect. Results showed that these factors impacted specifically on the initiation of expansion, as well as having a direct impact on suitability to expansion. The EBF outputs on distance of locality from road and river indicated that both factors had significance in Ae. albopictus expansion, which may be due to the greater transportability of Ae. albopictus eggs by vehicles, on rivers and in water catchment areas. Conversely, it is probable that geology does not impact significantly on Ae. albopictus expansion. Thus, altitude, slope, aspect, distance of locality from road, and distance of locality from river are the most significant non-climatic factors affecting expansions of Ae. albopictus.
Community education regarding Ae. albopictus and awareness campaigns as to home and garden sanitation and interventions from all levels of public, environmental health and vector control units, as well as private sector infestation control offering mosquito control to provide barrier treatments or other specific locality eradication methods is important. The efficiency and practicality of large-scale adulticiding should be researched, as well as determining the combination of factors which would demand the initiation of this control. Without ongoing strategies to prevent Ae. albopictus further expansion, the problem will have to be faced on an increased scale in the near future. Ongoing research has been examining controls involving genetic modification of the species, as well as RIDL (release of insects with dominant lethality) and the introduction of Wolbachia bacterium, an insect parasite (Walker, 2016).
Projected warmer winter temperatures, increasing gradually over the next few decades, will impact significantly on the potential for greater Ae. albopictus expansion of range in the southeastern and eastern USA. By implication, more people will live within Ae. albopictus range, and will potentially be subjected to more bites from the greater density of the species, thus being at greater risk of the posed arboviral threats of the species. At present, aside from small scale direct extermination of hatchings and prophylactic restriction of the specified semi-enclosed moist habitats of water and organic matter containers, by minimizing such habitats, no strategies or techniques of larger area control exists. Thus, public health agencies, particularly in regions with little or no broad anti-mosquito strategies and techniques, may find themselves in a vacuum, in terms of vector potential of Ae. albopictus and a novel pathogen.
Statistical modeling is advantageous for its simplicity and user friendly qualities throughout the suitability mapping process involved. It is also capable of processing large quantities of case or region-specific GIS data relatively quickly. Sustainable urban development is dependent on effective remedies to the potential health impacts of vector hazards that can reach epidemic proportions. Our study indexed potential non-climatic factors and delineated high risk regions, demonstrating an investigative and analytical approach as a foundation for the policy makers and public health networks. We reiterate that anticipating areas of potential establishment based on non-climatic factors is the priority practical approach, where a whole region is classified as suitable for Ae. albopictus range extension.