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248 results for “invasion impacts”
Impacts of Land Use on Japanese Barberry Invasion in Central Massachusetts 2005
Despite the recognized importance of historical factors in controlling many native species distributions, few studies have incorporated historical landscape changes into models of invasive species distribution and abundance. We explore the possibility that the current distribution of invasive species may reflect legacies of historical land use despite nearly a century of forest succession and subsequent disturbances. We evaluated the modern distribution and abundance of Berberis thunbergii DC. (Japanese barberry), a problematic non-native shrub in forests of the northeastern U.S., relative to two distinct periods of historical land use, modern forest harvesting activity, and environmental and edaphic characteristics. Species questions addressed in this study include: (1) Do patterns of historical land use influence modern barberry distribution and abundance? (2) What is the influence of disturbance type and timing relative to the timing of introduction on current barberry distribution and abundance? (3) Which disturbance, environmental and edaphic variables best predict modern barberry distribution and abundance? Japanese barberry occurred more frequently and was more abundant in sites historically cleared for agriculture than in historically wooded sites. This relationship was strongest for areas in agriculture in the early 20th century after barberry was introduced to the region. The strong relationship between modern distribution patterns and prior land use suggests historical colonization of abandoned agricultural lands and persistence through subsequent reforestation. Contrary to our expectations, recent forest harvesting did not influence the occurrence or abundance of barberry. Our results indicate that interpretations of both native community composition and modern plant invasions must consider the importance of historical landscape changes and the timing of species introduction along with current environmental and edaphic conditions.
Impacts of invasive species on food web energy pathways and quality, St. Lawrence River, 2018-2021.
This dataset contains field measurements collected between 2018 and 2021 from three fluvial lakes in the Upper St. Lawrence River (Canada), including both invaded systems (with dreissenid mussels and round goby) and uninvaded reference sites. Data include georeferenced sampling information (site, lake, latitude, longitude, month, year), water chemistry (total phosphorus, µg/L; conductivity, µS/cm), and habitat descriptors (substrate). Biological records encompass seston, macroinvertebrates, and fish. Fish data comprise species identity, sex, total length (mm), weight (g), relative weight index (Wr), and detailed fatty acid composition expressed as relative proportions (%) and concentrations (µg/mg), including essential LC-PUFAs (EPA, DHA), n-3 and n-6 polyunsaturated fatty acids. Stable isotope data are provided, including carbon (δ13C) and nitrogen (δ15N) ratios, C:N ratios, and isotopic baselines from pelagic (δ13Cpel, δ15Npel) and benthic (δ13Cben, δ15Nben) sources. Derived variables, such as pelagic diet proportion and trophic position, were calculated using the two-source mixing model described by Post (2002) (DOI: https://doi.org/10.1890/0012-9658(2002)083[0703:USITET]2.0.CO;2). These data provide a comprehensive resource for examining food web structure, energy pathways, and the ecological impacts of invasive species in large river ecosystems.
Impacts of black rat invasion on the primary rodent host of Lassa virus, Mastomys natalensis
<p>Shared here is code and data supporting the manuscript, "Reservoir displacement by an invasive rodent reduces Lassa virus zoonotic spillover risk."</p> <p>The project directory, which contains numerous large raster data files, was stored as a split zip archive to facilitate upload to Zenodo and consists of the files "rat_invasion.z01", "rat_invasion.z02", "rat_invasion.z03", and "rat_invasion.zip". Following download, these files may need to be decompressed using dedicated archiver software (such as The Unarchiver [https://theunarchiver.com/] on macOS). Note that the entire project repository is ~7 GB when uncompressed. The files shared here mirror the GitHub project repository (https://github.com/eveskew/rat_invasion) with the addition of the large environmental raster data in the "data/environmental" subdirectory.</p>
The impact of species phylogenetic relatedness on invasion varies distinctly along resource versus nonresource environmental gradients
<p><span>Understanding why certain plant communities are vulnerable to alien invasive species is essential to predicting and controlling invasion in a changing environment. Darwin's naturalization hypothesis suggests that non-native species should be more successful in communities where their close relatives are absent. Empirical tests of this hypothesis, however, have produced mixed results. Using plot-level data from natural forests along elevational transects covering strong environmental gradients, we examined whether the invasion of the globally invasive species <em>Ageratina adenophora</em> can be explained by environmental filtering and/or competition from closely related species linked to environmental gradients. Abundant precipitation, warm temperatures, open canopies, and postfire environments facilitated <em>A. adenophora</em> invasion, whereas resident taxonomic richness suppressed its invasion. Importantly, we found that invader-resident relatedness had a strong negative effect on invader cover under resource scarcity conditions (e.g., low water availability), but not under nonresource environmental stress conditions (e.g., low temperature). Our findings help reconcile the varied applicability of Darwin's naturalization hypothesis to biological invasions in a changing world.</span></p>
Figs. 1 and 2 in Studies of ambrosia beetles (Coleoptera: Curculionidae) in their native ranges help predict invasion impact
Figs. 1 and 2. Machilus (Lauraceae) trees in Huisun Forest, Taiwan, colonized by Xyleborus glabratus and Raffaelea lauricola. 1. Wood pieces excised from an injured but living tree. Staining is a reliable sign of R. lauricola establishment. 2. Injured trees showing symptoms of laurel wilt. Photographs by A. Black.
Fig. 2 in Impacts of crustacean invasions on parasite dynamics in aquatic ecosystems: A plea for parasite-focused studies
Fig. 2. Introduced hosts ‾ native parasites: hypothetical examples of the potential effects of invasive crustaceans on native parasites. Note that only a subsample of nonexclusive scenarios from a number of potential outcomes of biological invasion on native parasite dynamics is represented here. The hypothetical native parasite considered here has a two-host life cycle involving a definitive host predator and an intermediate host prey, transmission from the intermediate host to the definitive host requiring consumption of infected intermediate host prey. The variable sizes of squares, circles and diamonds represent relative intermediate and definitive hosts, and parasite abundances, respectively. During transmission, some parasites are unsuccessful and therefore lost from the system (parasite loss); the thickness of the arrows indicates the relative numbers that are either lost or successfully transmitted. The life cycle at the top represents the situation prior to the invasion, providing a benchmark for comparisons. (A) The invader is a suitable alternative intermediate host in which native parasite larvae can survive. However, the introduced host is also a poor transmission vector, due to low predation rate from the definitive host and/or failed host manipulation by the parasite, for example. Introduced hosts are thus more infected than their congeneric, native hosts only because of the accumulation of native parasite larvae that fail to get transmitted to the definitive host. This may in turn negatively affect parasite dynamics in native hosts as shown here. (B) The invader is again a suitable alternative intermediate host but also a good transmission vector to the definitive host, leading to greater infection risk for native definitive hosts. In this case, the invader positively influences parasite dynamics and may increase infection levels in definitive hosts, as shown here. In extreme cases, invasive hosts may be more efficient vectors for the parasite than native hosts and become key hosts. (C) The invader is not a suitable host but directly impacts native intermediate hosts, the transmission vector for the parasite, through predation and thus indirectly reduces native parasite abundance in native definitive hosts.
Fig. 1 in Impacts of crustacean invasions on parasite dynamics in aquatic ecosystems: A plea for parasite-focused studies
Fig. 1. Hypothetical examples of enemy release (A), dilution effect (B), parasite spillback (C) and spillover (D) following introduction of a non-native host in a recipient ecosystem, illustrating the fundamental differences among the different processes. The theoretical recipient ecosystem is here composed of a native host infected by a parasite with a simple life cycle and direct transmission, invaded by a congeneric non-native host infected with a co-introduced parasite with a similar life cycle, to simplify representation. The variable sizes of squares and diamonds represent relative host and parasite abundances, respectively. The thickness of the arrows represents transmission dynamics of the parasite and account for parasite loss during transmission. Enemy release (A) happens when the introduced species benefits from a reduction, or total loss as represented here, in parasitism as a result of invasion. This may in turn have drastic effects on invasion success and both native and invasive host abundances. Dilution effect (B) results from the failure of native parasites to use invasive hosts for successful reproduction and transmission. Native parasites may be unable to infect or be killed (as represented here) by the invasive host. Dilution may in turn decrease parasite transmission among native hosts and negatively affect parasite population dynamics. Parasite spillback (C) happens when invasive hosts acquire a native parasite that is already present in the native host population. Infected invasive hosts can then act as reservoirs of native parasites, potentially increasing infection levels in native hosts as represented here. Increased infection levels in the native host may in turn reduce native host abundance, compared to pre-invasion levels (not represented here). Parasite spillover (D) follows the co-introduction of non-native parasites with their invasive hosts and infection of native hosts by the introduced parasite. Infection of the native host can be maintained by the invasive host, which acts as a reservoir of infection, self-sustained if the parasite can reproduce in its novel host, or both as represented here. Infection of the native host by the introduced parasite can in turn influence host abundances, compared to pre-invasion levels. Note that in scenario D, the native host may or may not possess native parasites.
Fig. 3 in Impacts of crustacean invasions on parasite dynamics in aquatic ecosystems: A plea for parasite-focused studies
Fig. 3. Introduced parasites ‾ native/introduced hosts: hypothetical examples of the potential effects of invasive crustaceans on native parasites. Note that only a subsample of non-exclusive scenarios from a number of potential outcomes of non-native parasite introduction is represented here. The hypothetical non-native parasite considered here has a two-host life cycle involving a definitive host predator and an intermediate host prey, transmission from the intermediate host to the definitive host requiring consumption of infected intermediate host prey. The variable sizes of squares, circles and diamonds represent relative intermediate and definitive hosts, and parasite abundances, respectively. During transmission, some parasites are unsuccessful and therefore lost from the system (parasite loss); the thickness of the arrows indicates the relative numbers that are either lost or successfully transmitted. The life cycle at the top left represents the situation in the ecosystem of origin of the parasite, providing a benchmark for comparisons. Prior to the invasion, the hypothetical recipient ecosystem does not contain native parasites for simplification of representation. (A) The parasite is co-introduced with its intermediate host prey. The invasive parasite retains its original, co-introduced hosts and uses native definitive hosts to complete its life cycle. The situation represented here is the simplest one where the native predator exactly replaces the original definitive host of the parasite with no effect on either parasite dynamics or host abundance. However, parasite invasion may in turn negatively affect native predators and change parasite dynamics compared to that observed in the original ecosystem (shown at the top left). (B) The parasite is again cointroduced with its intermediate host prey. The invasive parasite retains its original, co-introduced hosts and uses native definitive hosts to complete its life cycle but also uses the native prey species as an alternative transmission vector. The introduced parasite may negatively influence native host abundance, thus influencing invasion success of its co-introduced host, as shown here. This may in turn lead to greater infection levels in definitive hosts in the recipient ecosystem than in the original ecosystem of the parasite (situation not represented here) (C) The non-native parasite is introduced without its original host (or this host does not survive translocation) but is subsequently included in the recipient food web. The novel parasite may in turn have drastic effects on intermediate and/or native hosts and reach higher infection levels in these novel hosts as represented here. However, a multitude of alternative scenarios are possible with as many outcomes in terms of parasite dynamics.
Fig. 4 in Forecasting the impact of an invasive macrophyte species in the littoral zone through aquatic insect species composition
Fig. 4. Comparison among Bray-Curtis dissimilarity indices of aquatic insect assemblages associated with white ginger lily banks and native vegetation profile in the littoral zone of a tropical reservoir in the Brazilian Savanna (Group 1, white ginger lily; Group 2, invaded forest; Group 3, native macrophyte; Group 4, riparian vegetation).
Fig. 2 in Forecasting the impact of an invasive macrophyte species in the littoral zone through aquatic insect species composition
Fig. 2. Comparison between ecological variables of aquatic insect assemblages associated with invasive white ginger lily bank and other native vegetation banks in the littoral zone of a tropical reservoir in the Brazilian Savanna (A, abundance; B, richness; C, Simpson diversity; IM, invasive macrophyte; IF, invaded forest; NM, native macrophyte; RV, riparian vegetation).
Fig. 1 in Forecasting the impact of an invasive macrophyte species in the littoral zone through aquatic insect species composition
Fig. 1. Location and characterization of vegetation profile banks of the Fazzari reservoir in the Brazilian Savanna (Cerrado Biome, Brazil).
Fig. 3 in Forecasting the impact of an invasive macrophyte species in the littoral zone through aquatic insect species composition
Fig. 3. Analyses of non-metric MDS of aquatic insect assemblages associated with white ginger lilY banks and native vegetation profiles in the littoral zone of a tropical reservoir in the Brazilian Savanna (●, white ginger lilY; ○, invaded forest; ∆, native macrohYte; ▲, riparian vegetation).
Data from: A tale of two studies: detection and attribution of the impacts of invasive plants in observational surveys
1.Short-term experiments cannot characterize how long-lived, invasive shrubs influence ecological properties that can be slow to change, including native diversity and soil fertility. Observational studies are thus necessary, but often suffer from methodological issues. 2.To highlight ways of improving the design and interpretation of observational studies that assess the impacts of invasive plants, we compare two studies of nutrient cycling and earthworms along two separate gradients of invasive shrub abundance. By considering the divergent sampling strategies and statistical analyses of these two studies, and interpreting their contradictory results in the context of other studies, we also aim to better describe the impacts of the focal invader, Rhamnus cathartica. 3.In a new study of a single site in Minnesota, we observed positive correlations between buckthorn abundance and soil pH, soil nutrient pools, nutrient fluxes through leaf litterfall, earthworm abundance, and root biomass. Multiple regression models showed these relationships persisted after accounting for variability in soil texture and tree species composition. For a separate, more expansive study in Illinois, other authors reported little to no correlation between buckthorn abundance and 10 soil properties, including earthworm abundance, pH, and nutrient concentrations. However, like many other studies, their regression models only assessed predictors related to invader abundance. R2 values for models of ecosystem properties ranged from 0-0.79 (adjusted-R2) for our study in Minnesota and from <0.05-0.16 (unadjusted) for the prior study in Illinois. 4.Differences in sampling error and use of predictor variables between the two studies likely explain the contrasting results. 5.Synthesis and applications. To reduce the uncertainty of conclusions from observational studies of invasive plants, future studies must ensure that heterogeneity of soils and vegetation is adequately accounted for in the sampling strategy and statistical analyses (e.g., analysis of covariance, multiple regression). Particular attention should be given to ecosystem properties with variability that likely predates the invader (e.g., geophysical features and tree community composition). In our study, effects of buckthorn on ecosystem properties were not only robust to the inclusion of potentially confounding predictors, but also consistent with expectations based on ecological stoichiometry and mass balance of element flow.
Data from: Quantifying and linking mechanism scenarios to invasive species impact
<p>Plant species invasion represents one of the major drivers of biodiversity change globally, yet there is confusion about the nature of non-indigenous species (NIS) impact. This stems from differing notions of what constitutes invasive species impact and the scales at which it should be assessed. At local scales, the mechanisms of impact on local competitors can be classified into four scenarios: 1) minimal impact from NIS inhabiting unique niches; 2) neutral impact spread across the community and proportional to NIS abundance; 3) targeted impact on a small number of competitors with overlapping niches; and 4) pervasive impact that is disproportionate to NIS abundance and caused by modifications that filter out other species. I developed a statistical test to distinguish these four mechanism scenarios based on plant community rank-abundance curves and then created a scale-independent standardized impact score. Using an example long-term dataset, that has high native plant diversity and an abundance gradient of the invasive vine, <em>Vincetoxicum rossicum</em>, I show that impact resulted in either targeted or pervasive extirpations. Regardless of whether NIS impact is neutral, targeted, or pervasive, the net outcome will be the homogenization of ecosystems and reduced biodiversity at larger scales, perhaps reducing ecosystem resilience. The framework and statistical evaluation of impact presented in this paper provide researchers and managers with an objective approach to quantifying NIS impact and prioritizing species for further management actions.</p>
Data from: Assessing the mechanisms and impacts of shrub invasion in forests: A meta-analysis
<ol> <li>The encroachment of invasive shrubs in forest understories can have detrimental effects on native plant recruitment. As a result, removal of invasive species is a common practice although long-lasting success is rare. In order to effectively conserve and manage invaded forests, it is crucial to understand the mechanisms that drive shrub invasion, i.e., high propagule pressure, low native resistance, and exploitation of empty niches.</li> <li>To gain a deeper understanding of the invasion process in forest ecosystems we conducted a meta-analysis of the work done in this topic. We collected data on invasive species and native community performance and on the abiotic conditions of forest understories under low and high levels of shrub invasion. We analyzed data from 124 articles that yielded 377 unique observations.</li> <li>Our results revealed that while invader performance did not vary by the mechanism of invasion, the impact on the native community was significantly detrimental when invasion occurred via low biotic resistance, and only marginally significant via propagule pressure. Invasive species performance was associated with increases in light availability, but not with other resources (soil water, or nutrients). When assessing impact on native performance as a function of invasive performance, results were again only significant under the low biotic resistance mechanism. Lastly, impacts were stronger when invasion took place by a single invader.</li> <li> <em>Synthesis and applications</em>: Taken together, these results suggest that restoration efforts should focus on (i) increasing the presence of strong native competitors or functionally diverse native communities, (ii) decreasing sources of invasive shrub propagules while keeping the canopies closed when invasion occurs via high propagule pressure, (iii) avoiding management techniques that degrade or diminish canopy cover, and (iv) prioritizing management of forest understories dominated by particularly impactful invasive shrubs.</li> </ol>
The impact of species phylogenetic relatedness on invasion varies distinctly along resource versus nonresource environmental gradients
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Data from: A tale of two studies: detection and attribution of the impacts of invasive plants in observational surveys
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Data from: Assessing the mechanisms and impacts of shrub invasion in forests: A meta-analysis
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Data from: Quantifying and linking mechanism scenarios to invasive species impact
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Extent, impacts, and drivers of oystershell scale invasions in aspen ecosystems in Arizona, USA 2020-2022
Invasive herbivores that kill foundation tree species pose a major threat to forest ecosystem sustainability. One important foundation tree species in the interior western United States is quaking aspen (Populus tremuloides), which is threatened by recent outbreaks of an invasive insect, oystershell scale (Lepidosaphes ulmi; OSS). OSS outbreaks were first reported in 2016, when OSS began causing dieback and mortality of aspen in wildland forest settings in northern Arizona. Since then, OSS has been observed in other locations across Arizona and in other western states, and recent studies in Arizona have highlighted the threat that OSS poses to aspen sustainability, warranting a comprehensive survey of OSS invasions and their impacts on aspen ecosystems. We sampled aspen populations across Arizona and addressed three questions: (1) What is the geographic extent of OSS in Arizona? (2) What impacts does OSS have on aspen? (3) Which biotic and abiotic factors influence OSS abundance? We found that OSS was widespread in central Arizona and had a negative impact on aspen forest health. OSS was associated with crown damage and tree mortality, especially of intermediate-sized, recruiting stems. Climate was the most important driver of plot-level OSS abundance, with warmer, drier conditions resulting in significantly more OSS. OSS was also associated with less recent fire, presence of ungulate management strategies such as fenced exclosures, and stands with a greater density of aspen saplings. We conclude that active management is required to suppress OSS populations and mitigate damage to aspen ecosystems, and we provide OSS monitoring and management recommendations based on our findings.
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