Invasive species

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Beavers from North America constitute an invasive species in Tierra del Fuego, where they have a substantial impact on landscape and local ecology through their dams.
Kudzu, a Japanese vine species invasive in the southeast United States, growing in Atlanta, Georgia
Vinca spreading in a garden[1]

An invasive species is a non-native species that spreads from the point of introduction and becomes abundant.[2]

The invasive species label attaches only to populations of species whose impact upon introduction has altered their new environment.[3] Although this impact can be beneficial, the term as most often used applies to introduced species that affect the invaded habitats and bioregions adversely, causing ecological, environmental, or economic damage.[4] This includes plant species labeled as "exotic pest plants" and "invasive exotics" growing in native plant communities.[5][6][7] The term is also used by land managers, botanists, researchers, horticulturalists, conservationists, and the public for noxious weeds.[8]

The term "invasive" is poorly defined and often very subjective,[9] and some broaden the term to include indigenous or "native" species that have colonized natural areas[9] – for example deer considered by some to be overpopulating their native zones and adjacent suburban gardens in the Northeastern and Pacific Coast regions of the United States.[10] The definition of "native" is also sometimes controversial. For example, the ancestors of Equus ferus (modern horses) evolved in North America and radiated to Eurasia before becoming locally extinct. Upon returning to North America in 1493, during their human-assisted migration, it is debatable as to whether they were native or exotic to the continent of their evolutionary ancestors.[11]

Invasion of long-established ecosystems by organisms is a natural phenomenon, but human-facilitated introductions have increased massively the rate, scale, and geographic range of invasion. For millennia, humans have served as both accidental and deliberate dispersal agents, beginning with our earliest migrations, accelerating in the age of discovery, and accelerating again with international trade.[12][13] Notable examples of invasive plant species include the kudzu vine, Andean pampas grass, and yellow starthistle. Animal examples include the New Zealand mud snail, feral pig, European rabbit, grey squirrel, domestic cat, carp, and ferret.[14][15][16] Some popular reference sources now name Homo sapiens, especially modern-age humans, as an invasive species,[17][18] but broad appreciation of human learning capacity and our behavioral potential and plasticity argues against any such fixed categorization.[19][20]

Causes[edit]

Typically, an introduced species must survive at low population densities before it becomes invasive in a new location.[21] At low population densities, it can be difficult for the introduced species to reproduce and maintain itself in a new location, so a species might reach a location multiple times before it becomes established. Repeated patterns of human movement, such as ships sailing to and from ports or cars driving up and down highways offer repeated opportunities for establishment (also known as a high propagule pressure).[22] Scientists include ecosystem and species factors among the mechanisms that, when combined, establish invasiveness in a newly introduced species.

Ecosystem-based mechanisms[edit]

In ecosystems, the amount of available resources and the extent to which those resources are used by organisms determine the effects of additional species on the ecosystem. In stable ecosystems, equilibrium exists in the use of available resources. These mechanisms describe a situation in which the ecosystem has suffered a disturbance, which changes the fundamental nature of the ecosystem.[23]

When changes such as a forest fire occur, normal succession favors native grasses and forbs. An introduced species that can spread faster than natives can use resources that would have been available to native species, squeezing them out. Nitrogen and phosphorus are often the limiting factors in these situations.[24]

Every species occupies a niche in its native ecosystem; some species fill large and varied roles, while others are highly specialized. Some invading species fill niches that are not used by native species, and they also can create new niches.[25] An example of this type can be found within the Lampropholis delicata species of skink. Invasion is more likely in ecosystems that are similar to the one in which the potential invader evolved.[12]

Ecosystem changes can alter species' distributions. For example, edge effects describe what happens when part of an ecosystem is disturbed as when land is cleared for agriculture. The boundary between remaining undisturbed habitat and the newly cleared land itself forms a distinct habitat, creating new winners and losers and possibly hosting species that would not thrive outside the boundary habitat.[26]

In 1958, Charles S. Elton[27] claimed that ecosystems with higher species diversity were less subject to invasive species because of fewer available niches. Other ecologists later pointed to highly diverse, but heavily invaded ecosystems and argued that ecosystems with high species diversity were more susceptible to invasion.[28]

This debate hinged on the spatial scale at which invasion studies were performed, and the issue of how diversity affects susceptibility remained unresolved as of 2011. Small-scale studies tended to show a negative relationship between diversity and invasion, while large-scale studies tended to show the reverse. The latter result may be a side-effect of invasives' ability to capitalize on increased resource availability and weaker species interactions that are more common when larger samples are considered.[29][30] However, this spatial scale dependent pattern of the effects of invasion on diversity does not seem to hold true when the invader is a vertebrate.[14]

The brown tree snake (Boiga irregularis)

Island ecosystems may be more prone to invasion because their species face few strong competitors and predators, or because their distance from colonizing species populations makes them more likely to have "open" niches.[31] An example of this phenomenon is the decimation of native bird populations on Guam by the invasive brown tree snake.[32] Conversely, invaded ecosystems may lack the natural competitors and predators that check invasives' growth in their native ecosystems.

On small islands, native birds may have become flightless because of the absence of predators prior to introductions. These birds cannot readily escape the danger brought to them by introduced predators. The tendency of rails in particular to evolve flightless forms on islands has made them vulnerable and has led to the disproportionate number of extinctions in that family.

The islands of Hawaii have many invasive species affecting the islands' native plants and animals. Invasive insects, plants, hoofed animals such as deer, goats and pigs endanger native plants, rosy wolfsnails from Africa feed on the island's native snails, and plants such as Australian tree fern and Miconia calvescens shade out native plants. Populations of introduced little fire ants in Hawaii can have major negative impacts on animals, crops, and humans. The veiled chameleon and the Jackson's chameleon have a great impact on the ecology of Hawaii.

In New Zealand the first invasive species were the dogs and rats brought by Polynesian settlers around 1300.[33][34] Cats, brought later by Europeans, have had a devastating effect upon the native birdlife, particularly as many New Zealand birds are flightless. Rabbits, introduced as a food source by sailors in the 1800s, have become a severe nuisance to farmers, notably in the South Island. Common gorse, originally a hedge plant in Britain, was introduced to New Zealand for the same purpose but grows aggressively and threatens to obliterate native plants in much of the country and is hence routinely eradicated. The native forests are heavily impacted by several species of deer from North America and Europe and by the Australian brushtail possum. These exotic species have all thrived in the New Zealand environment.

The colonization of the island of Madagascar has introduced exotic plant and animal species which have significantly altered the island's landscape.[35] This is a result of man-made disturbances to the ecosystems present. The most well-known disturbance is extensive logging.[36] This allows the invasion of non-native species as they establish in the spaces created. Some of the invasive plant species in Madagascar include prickly pear (Opuntia spp.) and silver wattle (Acacia dealbata).[37] The water hyacinth (Eichhornia crassipes), one of the most common invasive plant species in the world, has reached Madagascar over the last few decades.[38] This plant impacts Madagascar financially as a lot of resources are used in attempts to limit the spread. The plant occupies basins of lakes and other water bodies. It forms dense mats with its roots over the surfaces of water and limits light penetration which impacts aquatic organisms.[39] However, this plant is now being used in fertilizers and paper bags and for cleaning up biological waste.[39]

Invaded ecosystems may have experienced disturbance, typically human-induced.[12] Such a disturbance may give invasive species a chance to establish themselves with less competition from natives less able to adapt to a disturbed ecosystem.[21] Primary geomorphological effects of invasive plants are bioconstruction and bioprotection. For example, Kudzu Pueraria montana, a vine native to Asia, was widely introduced in the southeastern USA in the early 20th century to control soil erosion. The primary geomorphological effects of invasive animals are bioturbation, bioerosion, and bioconstruction. For example, invasions of the Chinese mitten crab Eriocheir sinensis have resulted in higher bioturbation and bioerosion rates.[40]

Species-based mechanisms[edit]

While all species compete to survive, invasive species appear to have specific traits or specific combinations of traits that allow them to outcompete native species. In some cases, the competition is about rates of growth and reproduction. In other cases, species interact with each other more directly.

Researchers disagree about the usefulness of traits as invasiveness markers. One study found that of a list of invasive and noninvasive species, 86% of the invasive species could be identified from the traits alone.[2] Another study found invasive species tended to have only a small subset of the presumed traits and that many similar traits were found in noninvasive species, requiring other explanations.[2][41][42] Common invasive species traits include the following:

An introduced species might become invasive if it can outcompete native species for resources such as nutrients, light, physical space, water, or food. If these species evolved under great competition or predation, then the new environment may host fewer able competitors, allowing the invader to proliferate quickly. Ecosystems which are being used to their fullest capacity by native species can be modeled as zero-sum systems in which any gain for the invader is a loss for the native. However, such unilateral competitive superiority (and extinction of native species with increased populations of the invader) is not the rule.[28][44] Invasive species often coexist with native species for an extended time, and gradually, the superior competitive ability of an invasive species becomes apparent as its population grows larger and denser and it adapts to its new location.

An invasive species might be able to use resources that were previously unavailable to native species, such as deep water sources accessed by a long taproot, or an ability to live on previously uninhabited soil types. For example, barbed goatgrass (Aegilops triuncialis) was introduced to California on serpentine soils, which have low water-retention, low nutrient levels, a high magnesium/calcium ratio, and possible heavy metal toxicity. Plant populations on these soils tend to show low density, but goatgrass can form dense stands on these soils and crowd out native species that have adapted poorly to serpentine soils.[45]

Invasive species might alter their environment by releasing chemical compounds, modifying abiotic factors, or affecting the behaviour of herbivores, creating a positive or negative impact on other species. Some species, like Kalanchoe daigremontana, produce allelopathic compounds, that might have an inhibitory effect on competing species, and influence some soil processes like carbon and nitrogen mineralization.[46] Other species like Stapelia gigantea facilitates the recruitment of seedlings of other species in arid environments by providing appropriate microclimatic conditions and preventing herbivory in early stages of development.[47]

Other examples are Centaurea solstitialis (yellow starthistle) and Centaurea diffusa (diffuse knapweed). These Eastern European noxious weeds have spread through the western and West Coast states. Experiments show that 8-hydroxyquinoline, a chemical produced at the root of C. diffusa, has a negative effect only on plants that have not co-evolved with it. Such co-evolved native plants have also evolved defenses. C. diffusa and C. solstitialis do not appear in their native habitats to be overwhelmingly successful competitors. Success or lack of success in one habitat does not necessarily imply success in others. Conversely, examining habitats in which a species is less successful can reveal novel weapons to defeat invasiveness.[48][49]

Changes in fire regimens are another form of facilitation. Bromus tectorum, originally from Eurasia, is highly fire-adapted. It not only spreads rapidly after burning but also increases the frequency and intensity (heat) of fires by providing large amounts of dry detritus during the fire season in western North America. In areas where it is widespread, it has altered the local fire regimen so much that native plants cannot survive the frequent fires, allowing B. tectorum to further extend and maintain dominance in its introduced range.[50]

Ecological facilitation also occurs where one species physically modifies a habitat in ways that are advantageous to other species. For example, zebra mussels increase habitat complexity on lake floors, providing crevices in which invertebrates live. This increase in complexity, together with the nutrition provided by the waste products of mussel filter-feeding, increases the density and diversity of benthic invertebrate communities.[51]

Studies of invasive species have shown that introduced species have great potential for rapid adaptation. This explains how many introduced species are able to establish and become invasive in new environments. In addition, the rate at which an invasive species can spread can be difficult to ascertain by biologists since population growth occurs geometrically, rather than linearly.[52] When bottlenecks and founder effects cause a great decrease in the population size and may constrict genetic variation,[53] the individuals begin to show additive variance as opposed to epistatic variance. This conversion can actually lead to increased variance in the founding populations which then allows for rapid adaptive evolution.[54] Following invasion events, selection may initially act on the capacity to disperse as well as physiological tolerance to the new stressors in the environment. Adaptation then proceeds to respond to the selective pressures of the new environment. These responses would most likely be due to temperature and climate change, or the presence of native species whether it be predator or prey.[55] Adaptations include changes in morphology, physiology, phenology, and plasticity.

Rapid adaptive evolution in these species leads to offspring that have higher fitness and are better suited for their environment. Intraspecific phenotypic plasticity, pre-adaptation and post-introduction evolution are all major factors in adaptive evolution.[56] Plasticity in populations allows room for changes to better suit the individual in its environment. This is key in adaptive evolution because the main goal is how to best be suited to the ecosystem to which the species has been introduced. The ability to accomplish this as quickly as possible will lead to a population with a very high fitness. Pre-adaptations and evolution after the initial introduction also play a role in the success of the introduced species. If the species has adapted to a similar ecosystem or contains traits that happen to be well suited to the area where it is introduced, it is more likely to fare better in the new environment. This, in addition to evolution that takes place after introduction, all determine if the species will be able to become established in the new ecosystem and if it will reproduce and thrive.

The enemy-release hypothesis states that the process of evolution has led to every ecosystem having an ecological balance. Any one species cannot occupy a majority of the ecosystem due to the presences of competitors, predators, and diseases. Introduced species moved to a novel habitat can become invasive when these controls - competitors, predators, and diseases - do not exist in the new ecosystem. The absence of appropriate controls leads to rapid population growth.[57]

Vectors[edit]

Non-native species have many vectors, including biogenic vectors, but most invasions are associated with human activity. Natural range extensions are common in many species, but the rate and magnitude of human-mediated extensions in these species tend to be much larger than natural extensions, and humans typically carry specimens greater distances than natural forces.[58]

An early human vector occurred when prehistoric humans introduced the Pacific rat (Rattus exulans) to Polynesia.[59]

Chinese mitten crab (Eriocheir sinensis)

Vectors include plants or seeds imported for horticulture. The pet trade moves animals across borders, where they can escape and become invasive. Organisms stow away on transport vehicles. Diseases may also be vectored by invasive insects such as the Asian citrus psyllid and the bacterial disease citrus greening.[60]

The arrival of invasive propagules to a new site is a function of the site's invasibility.[61]

Species have also been introduced intentionally. For example, to feel more "at home," American colonists formed "Acclimation Societies" that repeatedly imported birds that were native to Europe to North America and other distant lands. In 2008, U.S. postal workers in Pennsylvania noticed noises coming from inside a box from Taiwan; the box contained more than two dozen live beetles. Agricultural Research Service entomologists identified them as the rhinoceros beetle, Hercules beetle, and king stag beetle.[62] Because these species were not native to the U.S., they could have threatened native ecosystems. To prevent exotic species from becoming a problem in the U.S., special handling and permits are required when living materials are shipped from foreign countries. USDA programs such as Smuggling Interdiction and Trade Compliance (SITC) attempt to prevent exotic species outbreaks in America.

Many invasive species, once they are dominant in the area, are essential to the ecosystem of that area. If they are removed from the location it could be harmful to that area.[63]

Economics plays a major role in exotic species introduction. High demand for the valuable Chinese mitten crab is one explanation for the possible intentional release of the species in foreign waters.[64]

Within the aquatic environment[edit]

The development of maritime trade has rapidly affected the way marine organisms are transported within the ocean. Two ways marine organisms are transported to new environments are hull fouling and ballast water transport. In fact, Molnar et al. 2008 documented the pathways of hundreds of marine invasive species and found that shipping was the dominant mechanism for the transfer of invasive species.[65]

Cargo ship de-ballasting

Many marine organisms have the capacity to attach themselves to vessel hulls. Therefore, these organisms are easily transported from one body of water to another and are a significant risk factor for a biological invasion event.[66] Unfortunately, controlling for vessel hull fouling is voluntary and there are no regulations currently in place to manage hull fouling. However, the governments of California and New Zealand have announced more stringent control for vessel hull fouling within their respective jurisdictions.[67]

The other main vector for the transport of non-native aquatic species is ballast water. Ballast water taken up at sea and released in port by transoceanic vessels is the largest vector for non-native aquatic species invasions.[68][69] In fact, it is estimated that 10,000 different species, many of which are non-indigenous, are transported via ballast water each day.[70] Many of these species are considered harmful and can negatively affect their new environment. For example, freshwater zebra mussels, native to the Black, Caspian and Azov seas, most likely reached the Great Lakes via ballast water from a transoceanic vessel.[71] Zebra mussels outcompete other native organisms for oxygen and food, such as algae. Although the zebra mussel invasion was first noted in 1988, and a mitigation plan was successfully implemented shortly thereafter, the plan had a serious flaw or loophole, whereby ships loaded with cargo when they reached the Seaway were not tested because their ballast water tanks were empty. However, even in an empty ballast tank, there remains a puddle of water filled with organisms that could be released at the next port (when the tank is filled with water after unloading the cargo, the ship takes on ballast water which mixes with the puddles and then everything including the living organisms in the puddles is discharged at the next port).[68] Current regulations for the Great Lakes rely on ‘salinity shock’ to kill freshwater organisms left in ballast tanks.[72]

Even though ballast water regulations are in place to protect against potentially invasive species, there exists a loophole for organisms in the 10–50 micron size class. For organisms between 10 and 50 microns, such as certain types of phytoplankton, current regulations allow less than 10 cells per milliliter be present in discharge from treatment systems.[73] The discharge gets released when a ship takes on cargo at a port so the discharged water is not necessarily the same as the receiving body of water. Since many species of phytoplankton are less than 10 microns in size and reproduce asexually, only one cell released into the environment could exponentially grow into many thousands of cells over a short amount of time. This loophole could have detrimental effects to the environment. For example, some species in the genus Pseudo-nitzschia are smaller than 10 microns in width and contain domoic acid, a neurotoxin. If toxic Pseudo-nitzschia spp. are alive in ballast discharge and get released into their “new environment” they could cause domoic acid poisoning in shellfish, marine mammals and birds.[74] Fortunately, human deaths related to domoic acid poisoning have been prevented because of stringent monitoring programs that arose after a domoic acid outbreak in Canada in 1987.[74] Ballast water regulations need to be more rigorous to prevent future ramifications associated with the potential release of toxic and invasive phytoplankton.

Another important factor to consider about marine invasive species is the role of environmental changes associated with climate change, such as an increase in ocean temperature. There have been multiple studies suggesting an increase in ocean temperature will cause range shifts in organisms,[75][76] which could have detrimental effects on the environment as new species interactions emerge. For example, Hua and Hwang proposed that organisms in a ballast tank of a ship traveling from the temperature zone through tropical waters can experience temperature fluctuations as much as 20 °C.[77] To further examine the effects of temperature on organisms transported on hulls or in ballast water, Lenz et al. (2018) carried out study where they conducted a double heat stress experiment. Their results suggest that heat challenges organisms face during transport may enhance the stress tolerance of species in their non-native range by selecting for genetically adapted genotypes that will survive a second applied heat stress, such as increased ocean temperature in the founder population.[78] Due to the complexity of climate change induced variations, it is difficult to predict the nature of temperature-based success of non-native species in-situ. Since some studies have suggested increased temperature tolerance of “hijackers” on ships’ hulls or in ballast water, it is necessary to develop more comprehensive fouling and ballast water management plans in an effort to prevent against future possible invasions as environmental conditions continue to change around the world.

Effects of wildfire and firefighting[edit]

Invasive species often exploit disturbances to an ecosystem (wildfires, roads, foot trails) to colonize an area. Large wildfires can sterilize soils, while adding a variety of nutrients.[24] In the resulting free-for-all, formerly entrenched species lose their advantage, leaving more room for invasives. In such circumstances plants that can regenerate from their roots have an advantage. Non-natives with this ability can benefit from a low intensity fire burn that removes surface vegetation, leaving natives that rely on seeds for propagation to find their niches occupied when their seeds finally sprout.[50]

Wildfires often occur in remote areas, needing fire suppression crews to travel through pristine forest to reach the site. The crews can bring invasive seeds with them. If any of these stowaway seeds become established, a thriving colony of invasives can erupt in as few as six weeks, after which controlling the outbreak can need years of continued attention to prevent further spread. Also, disturbing the soil surface, such as cutting firebreaks, destroys native cover, exposes soil, and can accelerate invasions. In suburban and wildland-urban interface areas, the vegetation clearance and brush removal ordinances of municipalities for defensible space can result in excessive removal of native shrubs and perennials that exposes the soil to more light and less competition for invasive plant species.[citation needed]

Fire suppression vehicles are often major culprits in such outbreaks, as the vehicles are often driven on back roads overgrown with invasive plant species. The undercarriage of the vehicle becomes a prime vessel of transport. In response, on large fires, washing stations "decontaminate" vehicles before engaging in suppression activities.[citation needed] Large wildfires attract firefighters from remote places, further increasing the potential for seed transport.[citation needed]

Adverse effects[edit]

Invasive species can affect the invaded habitats and bioregions adversely, causing ecological, environmental, or economic damage.

Ecological[edit]

The European Union defines "Invasive Alien Species" as those that are, firstly, outside their natural distribution area, and secondly, threaten biological diversity.[79][80] Biotic invasion is considered one of the five top drivers for global biodiversity loss and is increasing because of tourism and globalization.[81][82] This may be particularly true in inadequately regulated fresh water systems, though quarantines and ballast water rules have improved the situation.[83]

An American alligator attacking a Burmese python in Florida; the Burmese python is an invasive species which is posing a threat to many indigenous species, including the alligator

Invasive species may drive local native species to extinction via competitive exclusion, niche displacement, or hybridisation with related native species. Therefore, besides their economic ramifications, alien invasions may result in extensive changes in the structure, composition and global distribution of the biota at sites of introduction, leading ultimately to the homogenisation of the world's fauna and flora and the loss of biodiversity.[84][85] It is difficult to unequivocally attribute extinctions to a species invasion. Although evidence is strong that the recent extinction of about 90 amphibian species can be traced to the chytrid fungus spread by international trade,[86] most scientific research has focused on animal invaders. Concern over the impacts of invasive species on biodiversity typically weighs the actual evidence (either ecological or economic) in relation to the potential risk.[87]

Land clearing and human habitation put significant pressure on local species. Disturbed habitats are prone to invasions that can have adverse effects on local ecosystems, changing ecosystem functions. A species of wetland plant known as ʻaeʻae in Hawaii (the indigenous Bacopa monnieri) is regarded as a pest species in artificially manipulated water bird refuges because it quickly covers shallow mudflats established for endangered Hawaiian stilt (Himantopus mexicanus knudseni), making these undesirable feeding areas for the birds.

Multiple successive introductions of different non-native species can have interactive effects; the introduction of a second non-native species can enable the first invasive species to flourish. Examples of this are the introductions of the amethyst gem clam (Gemma gemma) and the European green crab (Carcinus maenas). The gem clam was introduced into California's Bodega Harbor from the East Coast of the United States a century ago. It had been found in small quantities in the harbor but had never displaced the native clam species (Nutricola spp.). In the mid-1990s, the introduction of the European green crab, found to prey preferentially on the native clams, resulted in a decline of the native clams and an increase of the introduced clam populations.[88]

Invasive species can change the functions of ecosystems. For example, invasive plants can alter the fire regime (cheatgrass, Bromus tectorum), nutrient cycling (smooth cordgrass Spartina alterniflora), and hydrology (Tamarix) in native ecosystems.[13] Invasive species that are closely related to rare native species have the potential to hybridize with the native species. Harmful effects of hybridization have led to a decline and even extinction of native species.[89][90] For example, hybridization with introduced cordgrass, Spartina alterniflora, threatens the existence of California cordgrass (Spartina foliosa) in San Francisco Bay.[91] Invasive species cause competition for native species and because of this 400 of the 958 endangered species under the Endangered Species Act are at risk.[92]

Poster asking campers to not move firewood around, avoiding the spread of invasive species.

The unintentional introduction of forest pest species and plant pathogens can change forest ecology and damage the timber industry. Overall, forest ecosystems in the U.S. are widely invaded by exotic pests, plants, and pathogens.[93][94]

The Asian long-horned beetle (Anoplophora glabripennis) was first introduced into the U.S. in 1996, and was expected to infect and damage millions of acres of hardwood trees. As of 2005 thirty million dollars had been spent in attempts to eradicate this pest and protect millions of trees in the affected regions.[95] The woolly adelgid has inflicted damage on old-growth spruce, fir and hemlock forests and damages the Christmas tree industry.[96] And the chestnut blight fungus (Cryphonectria parasitica) and Dutch elm disease (Ophiostoma novo-ulmi) are two plant pathogens with serious impacts on these two species and on forest health.[97][98] Garlic mustard, Alliaria petiolata, is one of the most problematic invasive plant species in eastern North American forests. The characteristics of garlic mustard are slightly different from those of the surrounding native plants, which results in a highly successful species that is altering the composition and function of the native communities it invades. When garlic mustard invades the understory of a forest, it affects the growth rate of tree seedlings, which is likely to alter forest regeneration of impact forest composition in the future.[99]

Native species can be threatened with extinction[100] through the process of genetic pollution. Genetic pollution is unintentional hybridization and introgression, which leads to homogenization or replacement of local genotypes as a result of either a numerical or fitness advantage of the introduced species.[101] Genetic pollution occurs either through introduction or through habitat modification, where previously isolated species are brought into contact with the new genotypes. Invading species have been shown to adapt to their new environments in a remarkably short amount of time.[102] The population size of invading species may remain small for a number of years and then experience an explosion in population, a phenomenon known as "the lag effect".[103]

Hybrids resulting from invasive species interbreeding with native species can incorporate their genotypes into the gene pool over time through introgression. Similarly, in some instances a small invading population can threaten much larger native populations. For example, Spartina alterniflora was introduced in the San Francisco Bay and hybridized with native Spartina foliosa. The higher pollen count and male fitness of the invading species resulted in introgression that threatened the native populations due to lower pollen counts and lower viability of the native species.[104] Reduction in fitness is not always apparent from morphological observations alone. Some degree of gene flow is normal, and preserves constellations of genes and genotypes.[105][106] An example of this is the interbreeding of migrating coyotes with the red wolf, in areas of eastern North Carolina where the red wolf was reintroduced.[107] The end result was a decrease in stable breeding pairs of red wolf, which may further complicate the social stability of packs and reintroduction efforts.

Environmental[edit]

Invasive species and accompanying control efforts can have long term public health implications. For instance, pesticides applied to treat a particular pest species could pollute soil and surface water.[95] Encroachment of humans into previously remote ecosystems has exposed exotic diseases such as HIV[95] to the wider population. Introduced birds (e.g. pigeons), rodents and insects (e.g. mosquito, flea, louse and tsetse fly pests) can serve as vectors and reservoirs of human afflictions. Throughout recorded history, epidemics of human diseases, such as malaria, yellow fever, typhus, and bubonic plague, spread via these vectors.[27] A recent example of an introduced disease is the spread of the West Nile virus, which killed humans, birds, mammals, and reptiles.[108] The introduced Chinese mitten crabs are carriers of Asian lung fluke.[71] Waterborne disease agents, such as cholera bacteria (Vibrio cholerae), and causative agents of harmful algal blooms are often transported via ballast water.[109]

Economic[edit]

Globally, 1.4 trillion dollars are spent every year in managing and controlling invasive species.[57] Some invaders can negatively affect the economy of the local area. For example, in the Great Lakes Region the sea lamprey is an invasive species that acts as a predator. In its original habitat, the sea lamprey used co-evolution to act as a parasite without killing the host organism. However, in the Great Lakes Region, this co-evolutionary link is absent, so the sea lamprey acts as a predator and can consume up to 40 pounds of fish in its 12–18 month feeding period.[110] Sea lampreys prey on all types of large fish such as lake trout and salmon. The sea lampreys' destructive effects on large fish negatively affect the fishing industry and have helped cause the collapse of the population of some species.[110]

Economic costs from invasive species can be separated into direct costs through production loss in agriculture and forestry, and management costs. Estimated damage and control cost of invasive species in the U.S. alone amount to more than $138 billion annually.[95] Economic losses can also occur through loss of recreational and tourism revenues.[111] When economic costs of invasions are calculated as production loss and management costs, they are low because they do not consider environmental damage; if monetary values were assigned to the extinction of species, loss in biodiversity, and loss of ecosystem services, costs from impacts of invasive species would drastically increase.[95] The following examples from different sectors of the economy demonstrate the impact of biological invasions.

It is often argued that the key to reducing the costs of invasive species damage and management is early detection and rapid response,[112] meaning that incurring an initial cost of searching for and finding an invasive species and quickly controlling it, while the population is small, is less expensive that managing the invasive population when it is widespread and already causing damage. However, an intense search for the invader is only important to reduce costs in cases where the invasive species is (1) not frequently reintroduced into the managed area and (2) cost effective to search for and find.[113]

Alien invasive species Parthenium hysterophorus smothering native flora in Achanakmar Tiger Reserve, Bilaspur, Chhattisgarh, India.

Weeds reduce yield in agriculture, though they may provide essential nutrients. Some deep-rooted weeds can "mine" nutrients (see dynamic accumulator) from the subsoil and deposit them on the topsoil, while others provide habitat for beneficial insects or provide foods for pest species. Many weed species are accidental introductions that accompany seeds and imported plant material. Many introduced weeds in pastures compete with native forage plants, threaten young cattle (e.g., leafy spurge, Euphorbia esula) or are unpalatable because of thorns and spines (e.g., yellow starthistle). Forage loss from invasive weeds on pastures amounts to nearly US$1 billion in the U.S. alone.[95] A decline in pollinator services and loss of fruit production has been caused by honey bees infected by the invasive varroa mite. Introduced rats (Rattus rattus and R. norvegicus) have become serious pests on farms, destroying stored grains.[95] The introduction of leaf miner flies, including the American serpentine leaf miner, to California has also caused losses in California's floriculture industry, as the larvae of these invasive species feed on ornamental plants.[114]

Invasive plant pathogens and insect vectors for plant diseases can also suppress agricultural yields and nursery stock. Citrus greening is a bacterial disease vectored by the invasive Asian citrus psyllid (ACP). Because of the impacts of this disease on citrus crops, citrus is under quarantine and highly regulated in areas where ACP has been found.[60]

Invasive species can impact outdoor recreation, such as fishing, hunting, hiking, wildlife viewing, and water-based activities. They can damage a wide array of environmental services that are important to recreation, including, but not limited to, water quality and quantity, plant and animal diversity, and species abundance.[115] Eiswerth states, "very little research has been performed to estimate the corresponding economic losses at spatial scales such as regions, states, and watersheds". Eurasian watermilfoil (Myriophyllum spicatum) in parts of the US, fill lakes with plants complicating fishing and boating.[116] The very loud call of the introduced common coqui depresses real estate values in affected neighborhoods of Hawaii.[117]

Favorable effects[edit]

Invasive species have the potential to provide a suitable habitat or food source for other organisms. In areas where a native has become extinct or reached a point that it cannot be restored, non-native species can fill their role. An example of this is the Tamarisk, a non-native woody plant, and the Southwestern Willow Flycatcher, an endangered bird. 75% of Southwestern Willow Flycatchers were found to nest in these plants and their success was the same as the flycatchers that had nested in native plants. The removal of Tamarisk would be detrimental to Southwestern Willow Flycatcher as their native nesting sites are unable to be restored.[118]

The second way that non-native species can be beneficial is that they act as catalysts for restoration. This is because the presence of non-native species increases the heterogeneity and biodiversity in an ecosystem. This increase in heterogeneity can create microclimates in sparse and eroded ecosystems, which then promotes the growth and reestablishment of native species.

The last benefit of non-native species is that they provided ecosystem services.[118] The major example are pollinators. The American Honey bee was introduced in the rainforest[which?] to pollinate fragmented landscapes that native species cannot. Furthermore, non-native species can function as biocontrol agents to limit the effects of invasive species, such as the use of non-native species to control agricultural pests.[118] Asian oysters, for example, filter water pollutants better than native oysters to Chesapeake Bay. A study by the Johns Hopkins School of Public Health found the Asian oyster could significantly benefit the bay's deteriorating water quality.[119] Additionally, some species have invaded an area so long ago that they have found their own beneficial niche in the environment, a term referred to as naturalisation. For example, the bee L. leucozonium, shown by population genetic analysis to be an invasive species in North America,[120] has become an important pollinator of caneberry as well as cucurbit, apple trees, and blueberry bushes.[121]

Some invasions offer potential commercial benefits. For instance, silver carp and common carp can be harvested for human food and exported to markets already familiar with the product, or processed into pet foods, or mink feed. Water hyacinth can be turned into fuel by methane digesters,[122] and other invasive plants can also be harvested and utilized as a source of bioenergy.[123]

Eradication and study[edit]

Human behavioral potential and plasticity in species-environment interactions create possibilities for remediating adverse effects of species invasions.[124][19][20]

Reestablishing species[edit]

The field of island restoration has developed as a field of conservation biology and ecological restoration, a large part of which deals with the eradication of invasive species. A 2019 study suggests that if eradications of invasive animals were conducted on just 169 islands the survival prospects of 9.4% of the Earth's most highly threatened terrestrial insular vertebrates would be improved.[125]

Invasive vertebrate eradication on islands was found to align with the majority of United Nations Sustainable Development Goals (specifically Goal 15) and numerous associated targets such as marine and terrestrial biodiversity conservation, promotion of local and global partnerships, economic development, climate change mitigation, human health and sanitation and sustainable production and consumption.[126][127]

Rodents were carried to South Georgia, an island in the southern Atlantic Ocean with no permanent inhabitants, in the 18th century by sealing and whaling ships. They soon wrought havoc on the island's bird population, eating eggs and attacking chicks. In 2018, the South Georgia Island was declared free of invasive rodents after a multi-year extermination effort. Post-extermination, bird populations have rebounded, including populations of the South Georgia pipit and South Georgia pintail, two species found only on the island.[128][129]

Problematic exotic disease introductions in the past century or so include the chestnut blight which has almost eliminated the American chestnut tree from its forest habitat. Responses to increase the population of the American chestnut include creating blight resistant trees that can be reintroduced. This displays both the negative and the positive aspects of introduced species.

Taxon substitution[edit]

Non-native species can be introduced to fill an ecological engineering role that previously was performed by a native species now extinct. The procedure is known as taxon substitution.[118][130][131]

On many islands, tortoise extinction has resulted in dysfunctional ecosystems with respect to seed dispersal and herbivory. On the offshore islets of Mauritius, tortoises now extinct had served as the keystone herbivores. Introduction of the non-indigenous Aldabra giant tortoises on two islets in 2000 and 2007 has begun to restore ecological equilibrium.[132] The introduced tortoises are dispersing seeds of several native plants and are selectively grazing invasive plant species. Grazing and browsing are expected to replace ongoing intensive manual weeding, and the introduced tortoises are already breeding.

Invasivorism[edit]

Invasive species are flora and fauna whose introduction into a habitat disrupts the native eco-system. In response, Invasivorism is a movement that explores the idea of eating invasive species in order to control, reduce, or eliminate their populations. Chefs from around the world have begun seeking out and using invasive species as alternative ingredients.

In 2005 Chef Bun Lai of Miya's Sushi in New Haven, Connecticut created the first menu dedicated to the idea of using invasive species, during which time half the menus invasive species offerings were conceptual because invasive species were not yet commercially available.[133] Today, Miya's offers a plethora of invasive species such as Chesapeake blue catfish, Florida lionfish, Kentucky silver carp, Georgia cannonball jellyfish, and invasive edible plants such as Japanese knotweed and Autumn olive.[134][135][136][137]

Joe Roman, a Harvard and University of Vermont conservation biologist who is the recipient of the Rachel Carson Environmental award, is the editor and chief of Eat The Invaders, a website dedicated to encouraging people to eat invasive species as part of a solution to the problem.[138][139][133]

A dish that features whole fried invasive lionfish at Fish Fish of Miami, Florida

Skeptics point out that once a foreign species has entrenched itself in a new place—such as the Indo-Pacific lionfish that has now virtually taken over the waters of the Western Atlantic, Caribbean and Gulf of Mexico—eradication is almost impossible. Critics argue that encouraging consumption might have the unintended effect of spreading harmful species even more widely.[140]

Proponents of invasivorism argue that humans have the ability to eat away any species that it has an appetite for, pointing to the many animals which humans have been able to hunt to extinction—such as the Dodo bird, the Caribbean monk seal, and the passenger pigeon. Proponents of invasivorism also point to the success that Jamaica has had in significantly decreasing the population of lionfish by encouraging the consumption of the fish.[141]

In recent years, organizations including Reef Environmental Educational Foundation and the Institute for Applied Ecology, among others, have published cookbooks and recipes that include invasive species as ingredients.[142][143]

Terminology[edit]

Stage Characteristic
0 Propagules residing in a donor region
I Traveling
II Introduced
III Localized and numerically rare
IVa Widespread but rare
IVb Localized but dominant
V Widespread and dominant

While the study of invasive species can be done within many subfields of biology, the majority of research on invasive organisms has been within the field of ecology and geography where the issue of biological invasions is especially important. Much of the study of invasive species has been influenced by Charles Elton's 1958 book The Ecology of Invasion by Animals and Plants which drew upon the limited amount of research done within disparate fields to create a generalized picture of biological invasions.[144][145] Studies on invasive species remained sparse until the 1990s when research in the field experienced a large amount of growth which continues to this day.[145] This research, which has largely consisted of field observational studies, has disproportionately been concerned with terrestrial plants.[145] The rapid growth of the field has driven a need to standardize the language used to describe invasive species and events. Despite this, little standard terminology exists within the study of invasive species which itself lacks any official designation but is commonly referred to as "Invasion ecology" or more generally "Invasion biology".[144][145] This lack of standard terminology is a significant problem, and has largely arisen due to the interdisciplinary nature of the field which borrows terms from numerous disciplines such as agriculture, zoology, and pathology, as well as due to studies on invasive species being commonly performed in isolation of one another.[144]

In an attempt to avoid the ambiguous, subjective, and pejorative vocabulary that so often accompanies discussion of invasive species even in scientific papers, Colautti and MacIsaac proposed a new nomenclature system based on biogeography rather than on taxa.[9]

By discarding taxonomy, human health, and economic factors, this model focused only on ecological factors. The model evaluated individual populations rather than entire species. It classified each population based on its success in that environment. This model applied equally to indigenous and to introduced species, and did not automatically categorize successful introductions as harmful.

See also[edit]

References[edit]

Attibution[edit]

This article incorporates CC-BY-3.0 text from the reference[85]

Citations[edit]

  1. ^ "Global Compendium of Weeds: Vinca major". Hear.org. Retrieved February 13, 2020.
  2. ^ a b c Kolar, C.S. (2001). "Progress in invasion biology: predicting invaders". Trends in Ecology & Evolution. 16 (4): 199–204. doi:10.1016/S0169-5347(01)02101-2. PMID 11245943.
  3. ^ Davis, Mark A.; Thompson, Ken (2000). "Eight Ways to be a Colonizer; Two Ways to be an Invader: A Proposed Nomenclature Scheme for Invasion Ecology". Bulletin of the Ecological Society of America. Ecological Society of America. 81 (3): 226–230.
  4. ^ Ehrenfeld, Joan G. (2010). "Ecosystem Consequences of Biological Invasions". Annual Review of Ecology, Evolution, and Systematics. 41: 59–80. doi:10.1146/annurev-ecolsys-102209-144650. S2CID 85933159.
  5. ^ "Exotic Pest Plants of Greatest Ecological Concern in California" (PDF). Exotic Pest Plant Council. Archived from the original (PDF) on September 8, 2017. Retrieved October 4, 2010.
  6. ^ "National Invasive Species Information Center – What are Invasive Species?". USDA: National Agriculture Library. September 21, 2006. Retrieved September 1, 2007.
  7. ^ "Executive Order 13112 of February 3, 1999: Invasive Species". Federal Register. United States. 64 (25): 6183–86. 1999.
  8. ^ "Exotic Pest Plant Council" (PDF). p. 1. Archived from the original (PDF) on September 8, 2017. Retrieved October 4, 2010.
  9. ^ a b c Colautti, Robert I.; MacIsaac, Hugh J. (2004). "A neutral terminology to define 'invasive' species" (PDF). Diversity and Distributions. 10 (2): 135–141. doi:10.1111/j.1366-9516.2004.00061.x. Retrieved September 1, 2007.
  10. ^ Urbanek, Rachael E. (2011). "Urban and Suburban Deer Management by State Wildlife-Conservation Agencies". Wildlife Society Bulletin. 35 (3): 310–315. doi:10.1002/wsb.37. JSTOR wildsocibull2011.35.3.310.
  11. ^ Leidy, Joseph (March 5, 2012). "Ancient American Horses". Academy of Natural Sciences, Drexel University. Archived from the original on March 5, 2012. Retrieved January 10, 2019.
  12. ^ a b c d Williams, J. D. (1998). "Non-indigenous Species" (PDF). Status and Trends of the Nation's Biological Resources. Reston, Virginia: United States Geological Survey. pp. 117–29. ISBN 9780160532856.
  13. ^ a b Mack, R. (2000). "Biotic invasions: Causes, epidemiology, global consequences, and control". Ecological Applications. 10 (3): 689–710. doi:10.1890/1051-0761(2000)010[0689:BICEGC]2.0.CO;2. S2CID 711038.
  14. ^ a b Ivey, Matthew R.; Colvin, Michael; Strickland, Bronson K.; Lashley, Marcus A. (June 14, 2019). "Reduced vertebrate diversity independent of spatial scale following feral swine invasions". Ecology and Evolution. 9 (13): 7761–67. doi:10.1002/ece3.5360. PMC 6635915. PMID 31346438.
  15. ^ Krishna, Neal; Krishna, Vandana M.; Krishna, Ryan N.; Krishna, Sampath (February 2018). "The Invasiveness of the Genus Sylvilagus in Massachusetts and the Resulting Increase in Human Allergen Sensitization to Rabbits". Journal of Allergy and Clinical Immunology. 141 (2): AB236. doi:10.1016/j.jaci.2017.12.747.
  16. ^ Cove, Michael V.; Gardner, Beth; Simons, Theodore R.; Kays, Roland; O’Connell, Allan F. (February 1, 2018). "Free-ranging domestic cats (Felis catus) on public lands: estimating density, activity, and diet in the Florida Keys". Biological Invasions. 20 (2): 333–44. doi:10.1007/s10530-017-1534-x. S2CID 3536174.
  17. ^ Marean, Curtis W. (2015). "The Most Invasive Species of All". Scientific American. 313 (2): 32–39. Bibcode:2015SciAm.313b..32M. doi:10.1038/scientificamerican0815-32. JSTOR 26046104. PMID 26349141.
  18. ^ Rafferty, John P. (2015). "Invasive species". Encyclopedia Britannica. Retrieved August 18, 2020. ...[M]odern humans are among the most successful invasive species.
  19. ^ a b Root‐Bernstein, Meredith; Ladle, Richard (2019). "Ecology of a widespread large omnivore, Homo sapiens, and its impacts on ecosystem processes". Ecology and Evolution. 9 (19): 10874–94. doi:10.1002/ece3.5049. PMC 6802023. PMID 31641442. S2CID 203370925.
  20. ^ a b Garrido-Pérez, Edgardo I.; Tella Ruiz, David (2016). "Homo sapiens (Primates: Hominidae): an invasive species or even worse? A challenge for strengthening ecology and conservation biology. (Translated from Spanish)". Puente Biologico (in Spanish) (8): 43–55. Retrieved August 19, 2020.
  21. ^ a b Tilman, D. (2004). "Niche tradeoffs, neutrality, and community structure: A stochastic theory of resource competition, invasion, and community assembly". Proceedings of the National Academy of Sciences. 101 (30): 10854–10861. Bibcode:2004PNAS..10110854T. doi:10.1073/pnas.0403458101. PMC 503710. PMID 15243158.
  22. ^ Verling, E. (2005). "Supply-side invasion ecology: characterizing propagule pressure in coastal ecosystems". Proceedings of the Royal Society B. 272 (1569): 1249–1256. doi:10.1098/rspb.2005.3090. PMC 1564104. PMID 16024389.
  23. ^ Byers, J.E. (2002). "Impact of non-indigenous species on natives enhanced by anthropogenic alteration of selection regimes". Oikos. 97 (3): 449–458. doi:10.1034/j.1600-0706.2002.970316.x. S2CID 4176015.
  24. ^ a b Davis, M.A.; Grime, J.P.; Thompson, K. (2000). "Fluctuating resources in plant communities: A general theory of invisibility". Journal of Ecology. 88 (3): 528–534. doi:10.1046/j.1365-2745.2000.00473.x. S2CID 14573817.
  25. ^ Fath, Brian D. (2008). Encyclopedia of Ecology. Amsterdam, The Netherlands: Elsevier Science; 1 edition. p. 1089. ISBN 978-0444520333.
  26. ^ Alverson, William S.; Waller, Donald M.; Solheim, Stephen L. (1988). "Forests Too Deer: Edge Effects in Northern Wisconsin". Conservation Biology. 2 (4): 348–358. doi:10.1111/j.1523-1739.1988.tb00199.x. JSTOR 2386294.
  27. ^ a b Elton, C.S. (2000) [1958]. The Ecology of Invasions by Animals and Plants. Foreword by Daniel Simberloff. Chicago: University of Chicago Press. p. 196. ISBN 978-0-226-20638-7.
  28. ^ a b Stohlgren, T.J.; Binkley, D.; Chong, G.W.; Kalkhan, M.A.; Schell, L.D.; Bull, K.A.; Otsuki, Y.; Newman, G.; Bashkin, M.; Son, Y. (1999). "Exotic plant species invade hot spots of native plant diversity". Ecological Monographs. 69: 25–46. doi:10.1890/0012-9615(1999)069[0025:EPSIHS]2.0.CO;2. S2CID 73640245.
  29. ^ Byers, J.E. (2003). "Scale dependent effects of biotic resistance to biological invasion". Ecology. 84 (6): 1428–1433. doi:10.1890/02-3131. S2CID 4192256.
  30. ^ Levine, J. M. (2000). "Species diversity and biological invasions: Relating local process to community pattern". Science. 288 (5467): 852–854. Bibcode:2000Sci...288..852L. doi:10.1126/science.288.5467.852. PMID 10797006. S2CID 7363143.
  31. ^ Stachowicz, J.J. (2005). "Species invasions and the relationships between species diversity, community saturation, and ecosystem functioning". In D.F. Sax; J.J. Stachowicz; S.D. Gaines (eds.). Species Invasions: Insights into Ecology, Evolution, and Biogeography. Sunderland, Massachusetts: Sinauer Associates. ISBN 978-0-87893-811-7.
  32. ^ Invasive Species: Animals – Brown Tree Snake, National Agricultural Library, United States Department of Agriculture, Retrieved August 31, 2010
  33. ^ Howe, K. R. (2003). The Quest for Origins. p. 179. ISBN 0-14-301857-4.
  34. ^ Rat remains help date New Zealand's colonisation. New Scientist. June 4, 2008. Retrieved June 23, 2008.
  35. ^ Goodman, Steven M. (1997). The birds of southeastern Madagascar. Fieldiana. Chicago, Ill.: Field Museum of Natural History. doi:10.5962/bhl.title.3415.
  36. ^ Brown, K. A.; Gurevitch, J. (April 5, 2004). "Long-term impacts of logging on forest diversity in Madagascar". Proceedings of the National Academy of Sciences. 101 (16): 6045–6049. Bibcode:2004PNAS..101.6045B. doi:10.1073/pnas.0401456101. ISSN 0027-8424. PMC 395920. PMID 15067121.
  37. ^ Kull, CA; Tassin, J; Carriere, SM (February 26, 2015). "Approaching invasive species in Madagascar". Madagascar Conservation & Development. 9 (2): 60. doi:10.4314/mcd.v9i2.2. ISSN 1662-2510.
  38. ^ Villamagna, A. M.; Murphy, B. R. (February 2010). "Ecological and socio-economic impacts of invasive water hyacinth (Eichhornia crassipes): a review". Freshwater Biology. 55 (2): 282–298. doi:10.1111/j.1365-2427.2009.02294.x. ISSN 0046-5070.
  39. ^ a b Rakotoarisoa, T. F.; Richter, T.; Rakotondramanana, H.; Mantilla-Contreras, J. (December 2016). "Turning a Problem Into Profit: Using Water Hyacinth (Eichhornia crassipes) for Making Handicrafts at Lake Alaotra, Madagascar". Economic Botany. 70 (4): 365–379. doi:10.1007/s12231-016-9362-y. ISSN 0013-0001. S2CID 18820290.
  40. ^ Fei, S. (2015). "Biogeomorphic Impacts of Invasive Species". Annual Review of Ecology, Evolution, and Systematics. 45: 69–87. doi:10.1146/annurev-ecolsys-120213-091928. S2CID 85870208.
  41. ^ Thebaud, C. (1996). "Assessing why two introduced Conyza differ in their ability to invade Mediterranean old fields". Ecology. 77 (3): 791–804. doi:10.2307/2265502. JSTOR 2265502.
  42. ^ Reichard, S.H. (1997). "Predicting invasions of woody plants introduced into North America". Conservation Biology. 11 (1): 193–203. doi:10.1046/j.1523-1739.1997.95473.x. PMC 7162396. S2CID 29816498.
  43. ^ Ewell, J.J. (1999). "Deliberate introductions of species: Research needs – Benefits can be reaped, but risks are high". BioScience. 49 (8): 619–630. doi:10.2307/1313438. JSTOR 1313438.
  44. ^ Sax, D.F. (2002). "Species Invasions Exceed Extinctions on Islands Worldwide: A Comparative Study of Plants and Birds". American Naturalist. 160 (6): 766–783. doi:10.1086/343877. PMID 18707464. S2CID 8628360.
  45. ^ Huenneke, L. (1990). "Effects of soil resources on plant invasion and community structure in California (USA) serpentine grassland". Ecology. 71 (2): 478–491. doi:10.2307/1940302. JSTOR 1940302. S2CID 53967932.
  46. ^ Herrera, Ileana; Ferrer-Paris, José R.; Benzo, Diana; Flores, Saúl; García, Belkis; Nassar, Jafet M. (2018). "An Invasive Succulent Plant (Kalanchoe daigremontiana) Influences Soil Carbon and Nitrogen Mineralization in a Neotropical Semiarid Zone". Pedosphere. 28 (4): 632–643. doi:10.1016/S1002-0160(18)60029-3.
  47. ^ Herrera, Ileana; Ferrer-Paris, José R.; Hernández-Rosas, José I.; Nassar, Jafet M. (2016). "Impact of two invasive succulents on native-seedling recruitment in Neotropical arid environments". Journal of Arid Environments. 132: 15–25. Bibcode:2016JArEn.132...15H. doi:10.1016/j.jaridenv.2016.04.007.
  48. ^ Hierro, J.L. (2003). "Allelopathy and exotic plant invasion". Plant and Soil. 256 (1): 29–39. doi:10.1023/A:1026208327014. S2CID 40416663.
  49. ^ Vivanco, J.M.; Bais, H.P.; Stermitz, F.R.; Thelen, G.C.; Callaway, R.M. (2004). "Biogeographical variation in community response to root allelochemistry: Novel weapons and exotic invasion". Ecology Letters. 7 (4): 285–292. doi:10.1111/j.1461-0248.2004.00576.x.
  50. ^ a b Brooks, M.L.; D'Antonio, C.M.; Richardson, D.M.; Grace, J.B.; Keeley, J.E.; DiTomaso, J.M.; Hobbs, R.J.; Pellant, M.; Pyke, D. (2004). "Effects of invasive alien plants on fire". BioScience. 54 (7): 677–688. doi:10.1641/0006-3568(2004)054[0677:EOIAPO]2.0.CO;2.
  51. ^ Silver Botts, P.; Patterson, B.A.; Schlosser, D. (1996). "Zebra mussel effects on benthic invertebrates: Physical or biotic?". Journal of the North American Benthological Society. 15 (2): 179–184. doi:10.2307/1467947. JSTOR 1467947.
  52. ^ Keddy, Paul A. (2017). Plant Ecology. Cambridge University Press. p. 343. ISBN 978-1-107-11423-4.
  53. ^ Xu, Cheng-Yuan; Tang, Shaoqing; Fatemi, Mohammad; Gross, Caroline L.; Julien, Mic H.; Curtis, Caitlin; van Klinken, Rieks D. (September 1, 2015). "Population structure and genetic diversity of invasive Phyla canescens: implications for the evolutionary potential". Ecosphere. 6 (9): art162. doi:10.1890/ES14-00374.1.
  54. ^ Prentis, Peter (2008). "Adaptive evolution in invasive species". Trends in Plant Science. 13 (6): 288–294. doi:10.1016/j.tplants.2008.03.004. PMID 18467157.
  55. ^ Lee, Carol Eunmi (2002). "Evolutionary genetics of invasive species". Trends in Ecology & Evolution. 17 (8): 386–391. doi:10.1016/s0169-5347(02)02554-5.
  56. ^ Zenni, R.D. (2013). "Adaptive Evolution and Phenotypic Plasticity During Naturalization and Spread of Invasive Species: Implications for Tree Invasion Biology". Biological Invasions. 16 (3): 635–644. doi:10.1007/s10530-013-0607-8. S2CID 82590.
  57. ^ a b Amstutz, Lisa J (2018). Invasive Species. Minneapolis, MN: Abdo Publishing. pp. 8–10. ISBN 9781532110245.
  58. ^ Cassey, P (2005). "Concerning Invasive Species: Reply to Brown and Sax". Austral Ecology. 30 (4): 475–480. doi:10.1111/j.1442-9993.2005.01505.x.
  59. ^ Matisoo-Smith, E. (1998). "Patterns of prehistoric human mobility in Polynesia indicated by mtDNA from the Pacific rat". Proceedings of the National Academy of Sciences of the United States of America. 95 (25): 15145–15150. Bibcode:1998PNAS...9515145M. doi:10.1073/pnas.95.25.15145. PMC 24590. PMID 9844030.
  60. ^ a b "Citrus Greening." Invasive Species Program – Pest Alerts. Clemson University – DPI (2013). Accessed May 24, 2013.
  61. ^ Leung, B. (2007). "The risk of establishment of aquatic invasive species: joining invasibility and propagule pressure". Proceedings of the Royal Society B. 274 (1625): 2733–2739. doi:10.1098/rspb.2007.0841. PMC 2275890. PMID 17711834.
  62. ^ "Our Invaluable Invertebrate Collections". Ars.usda.gov. Retrieved May 17, 2011.
  63. ^ Zavaleta, Erika; Hobbs, Richard; Mooney, Harold (August 2001). "Viewing invasive species removal in a whole-ecosystem context" (PDF). Trends in Ecology & Evolution. 16 (8): 458. doi:10.1016/s0169-5347(01)02194-2. Retrieved October 21, 2017.
  64. ^ Seinfeld, John H. (2016). Marine Pollution and Climate Change. John Wiley & Sons.
  65. ^ Molnar, Jennifer L; Gamboa, Rebecca L; Revenga, Carmen; Spalding, Mark D (2008). "Assessing the global threat of invasive species to marine biodiversity". Frontiers in Ecology and the Environment. 6 (9): 485–492. doi:10.1890/070064. S2CID 84918861.
  66. ^ Drake, John (2007). "Hull fouling is a risk factor for intercontinental species exchange in aquatic ecosystems". Aquatic Invasions. 2 (2): 121–131. doi:10.3391/ai.2007.2.2.7.
  67. ^ "Biofouling moves up the regulatory agenda – GARD". www.gard.no. Retrieved September 19, 2018.
  68. ^ a b Egan, Dan (October 31, 2005). "Noxious cargo". Journal Sentinel. Archived from the original on October 21, 2011. Retrieved April 22, 2017.
  69. ^ Xu, Jian; Wickramarathne, Thanuka L.; Chawla, Nitesh V.; Grey, Erin K.; Steinhaeuser, Karsten; Keller, Reuben P.; Drake, John M.; Lodge, David M. (August 24, 2014). Improving management of aquatic invasions by integrating shipping network, ecological, and environmental data: data mining for social good. ACM. pp. 1699–1708. doi:10.1145/2623330.2623364. ISBN 9781450329569. S2CID 2371978.
  70. ^ Streftaris, N; Zenetos, Argyro; Papathanassiou, Enangelos (2005). "Globalisation in marine ecosystems: The story of non-indigenous marine species across European seas". Oceanography and Marine Biology. 43: 419–453.
  71. ^ a b Aquatic invasive species. A Guide to Least-Wanted Aquatic Organisms of the Pacific Northwest. 2001. University of Washington
  72. ^ Great Lake Commission. "Status of Ballast Water Discharge Regulations in the Great Lakes Region" (PDF).
  73. ^ USCG. "Ballast Water Management for Control of Non-Indigenous Species in Waters of the United States" (PDF).
  74. ^ a b Trainer, Vera L.; Bates, Stephen S.; Lundholm, Nina; Thessen, Anne E.; Cochlan, William P.; Adams, Nicolaus G.; Trick, Charles G. (2012). "Pseudo-nitzschia physiological ecology, phylogeny, toxicity, monitoring and impacts on ecosystem health". Harmful Algae. 14: 271–300. doi:10.1016/j.hal.2011.10.025. hdl:1912/5118.
  75. ^ Occhipinti-Ambrogi, Anna (2007). "Global change and marine communities: Alien species and climate change". Marine Pollution Bulletin. 55 (7–9): 342–352. doi:10.1016/j.marpolbul.2006.11.014. PMID 17239404.
  76. ^ Rahel, Frank J.; Olden, Julian D. (2008). "Assessing the effects of climate change on aquatic invasive species". Conservation Biology. 22 (3): 521–533. doi:10.1111/j.1523-1739.2008.00950.x. PMID 18577081. S2CID 313824.
  77. ^ Hua, J.; Hwang, W.H. (2012). "Effects of voyage routing on the survival of microbes in ballast water". Ocean Engineering. 42: 165–175. doi:10.1016/j.oceaneng.2012.01.013.
  78. ^ Lenz, Mark; Ahmed, Yasser; Canning-Clode, João; Díaz, Eliecer; Eichhorn, Sandra; Fabritzek, Armin G.; da Gama, Bernardo A. P.; Garcia, Marie; von Juterzenka, Karen (May 24, 2018). "Heat challenges can enhance population tolerance to thermal stress in mussels: a potential mechanism by which ship transport can increase species invasiveness". Biological Invasions. 20 (11): 3107–3122. doi:10.1007/s10530-018-1762-8. S2CID 53082967.
  79. ^ "Communication From The Commission To The Council, The European Parliament, The European Economic And Social Committee And The Committee Of The Regions Towards An EU Strategy On Invasive Species" (PDF). Retrieved May 17, 2011.
  80. ^ Lakicevic, Milena; Mladenovic, Emina (2018). "Non-native and invasive tree species - their impact on biodiversity loss". Zbornik Matice Srpske Za Prirodne Nauke (134): 19–26. doi:10.2298/ZMSPN1834019L.
  81. ^ National Research Council (US) Committee on the Scientific Basis for Predicting the Invasive Potential of Nonindigenous Plants Plant Pests in the United States (2002). Read "Predicting Invasions of Nonindigenous Plants and Plant Pests" at NAP.edu. doi:10.17226/10259. ISBN 978-0-309-08264-8. PMID 25032288.
  82. ^ Lewis, Simon L.; Maslin, Mark A. (2015). "Defining the Anthropocene". Nature. 519 (7542): 171–180. Bibcode:2015Natur.519..171L. doi:10.1038/nature14258. PMID 25762280. S2CID 205242896.
  83. ^ Millennium Ecosystem Assessment (2005). "Ecosystems and Human Well-being: Biodiversity Synthesis" (PDF). World Resources Institute.
  84. ^ Baiser, Benjamin; Olden, Julian D.; Record, Sydne; Lockwood, Julie L.; McKinney, Michael L. (2012). "Pattern and process of biotic homogenization in the New Pangaea". Proceedings of the Royal Society B: Biological Sciences. 279 (1748): 4772–4777. doi:10.1098/rspb.2012.1651. PMC 3497087. PMID 23055062.
  85. ^ a b Odendaal, L. J.; Haupt, T. M.; Griffiths, C. L. (2008). "The alien invasive land snail Theba pisana in the West Coast National Park: Is there cause for concern?"". Koedoe. 50 (1): 93–98. doi:10.4102/koedoe.v50i1.153.
  86. ^ Fisher, Matthew C.; Garner, Trenton W. J. (2020). "Chytrid fungi and global amphibian declines". Nature Reviews Microbiology. 18 (6): 332–343. doi:10.1038/s41579-020-0335-x. PMID 32099078. S2CID 211266075.
  87. ^ Baofu, Peter (2013). Beyond Natural Resources to Post-Human Resources: Towards a New Theory of diversity and discontinuity. Cambridge Scholars Publishing; 1st Unabridged edition. p. 17. ISBN 978-1443844536.
  88. ^ Grosholz, E.D. (2005). "Recent biological invasion may hasten invasional meltdown by accelerating historical introductions". Proceedings of the National Academy of Sciences. 102 (4): 1088–1091. Bibcode:2005PNAS..102.1088G. doi:10.1073/pnas.0308547102. PMC 545825. PMID 15657121.
  89. ^ Hawkes, C.V. (2005). "Plant invasion alters nitrogen cycling by modifying the soil nitrifying community". Ecology Letters. 8 (9): 976–985. doi:10.1111/j.1461-0248.2005.00802.x.
  90. ^ Rhymer, J. M.; Simberloff, D. (1996). "Extinction by hybridization and introgression". Annual Review of Ecology and Systematics. 27 (1): 83–109. doi:10.1146/annurev.ecolsys.27.1.83.
  91. ^ Ayres, D.; et al. (2004). "Spread of exotic cordgrasses and hybrids (Spartina sp.) in the tidal marshes of San Francisco Bay, California". USA Biological Invasions. 6 (2): 221–231. doi:10.1023/B:BINV.0000022140.07404.b7. S2CID 24732543.
  92. ^ Primtel, David (2005). "Update on the environmental and economic costs associated with alien-invasive species in the United States". Ecological Economics. 52 (3): 273–288. doi:10.1016/j.ecolecon.2004.10.002.
  93. ^ Liebhold, S.; et al. (2013). "A highly aggregated geographical distribution of forest pest invasions in the USA". Diversity and Distributions. 19 (9): 1208–1216. doi:10.1111/ddi.12112.
  94. ^ Oswalt, C.; et al. (2015). "A subcontinental view of forest plant invasions". NeoBiota. 24: 49–54. doi:10.3897/neobiota.24.8378.
  95. ^ a b c d e f g Pimentel, D.; R., Zuniga; Morrison, D (2005). "Update on the environmental and economic costs associated with alien-invasive species in the United States". Ecological Economics. 52 (3): 273–288. doi:10.1016/j.ecolecon.2004.10.002.
  96. ^ Balsam woolly aphid Adelges piceae (Ratzeburg) ForestPests.org (March 3, 2005) Retrieved on September 1, 2007.
  97. ^ Schlarbaum, Scott E., Frederick Hebard, Pauline C. Spaine, and Joseph C. Kamalay. (1998) "Three American Tragedies: Chestnut Blight, Butternut Canker, and Dutch Elm Disease'. In: Britton, Kerry O., Ed. Exotic Pests of Eastern Forests Conference Proceedings; 1997 April 8–10; Nashville, TN. U.S. Forest Service and Tennessee Exotic Pest Plant Council., pp. 45–54.
  98. ^ Schlarbaum, Scott E.; Hebard, Frederick; Spaine, Pauline C.; Kamalay, Joseph C. (1997). "Three American Tragedies: Chestnut Blight, Butternut Canker and Dutch Elm Disease". (originally published via: Proceedings: Exotic Pests of Eastern Forests; (1997 April 8–10); Nashville, TN. Tennessee Exotic Pest Plant Council: 45–54.). Southern Research Station, Forest Service, United States Department of Agriculture. Retrieved June 22, 2012.
    Alternative link and additional publication citation information: Tree Search, US Forest Service, USDA. http://www.treesearch.fs.fed.us/pubs/745
  99. ^ Rodger, Vikki; Stinson, Kristin; Finzi, Adrian (2008). "Ready or Not, Garlic Mustard Is Moving In: Alliaria petiolata as a Member of Eastern North American Forests". BioScience. 58 (5): 5. doi:10.1641/b580510.
  100. ^ Mooney, HA; Cleland, EE (2001). "The evolutionary impact of invasive species". Proceedings of the National Academy of Sciences of the United States of America. 98 (10): 5446–51. Bibcode:2001PNAS...98.5446M. doi:10.1073/pnas.091093398. PMC 33232. PMID 11344292.
  101. ^ "Glossary: definitions from the following publication: Aubry, C., R. Shoal and V. Erickson. 2005. Grass cultivars: their origins, development, and use on national forests and grasslands in the Pacific Northwest. USDA Forest Service. 44 pages, plus appendices.; Native Seed Network (NSN), Institute for Applied Ecology, 563 SW Jefferson Ave, Corvallis, OR 97333, USA". Nativeseednetwork.org. Archived from the original on February 22, 2006. Retrieved May 17, 2011.
  102. ^ Mooney, H. A.; Cleland, E. E. (May 8, 2001). "The evolutionary impact of invasive species". Proceedings of the National Academy of Sciences. 98 (10): 5446–5451. Bibcode:2001PNAS...98.5446M. doi:10.1073/pnas.091093398. PMC 33232. PMID 11344292.
  103. ^ Mack, Richard N.; Simberloff, Daniel; Mark Lonsdale, W.; Evans, Harry; Clout, Michael; Bazzaz, Fakhri A. (June 1, 2000). "Biotic Invasions: Causes, Epidemiology, Global Consequences, and Control". Ecological Applications. 10 (3): 689–710. doi:10.1890/1051-0761(2000)010[0689:BICEGC]2.0.CO;2. S2CID 711038.
  104. ^ Anttila, C. K.; King, R. A.; Ferris, C.; Ayres, D. R.; Strong, D. R. (2000). "Reciprocal hybrid formation of Spartina in San Francisco Bay". Molecular Ecology. 9 (6): 765–770. doi:10.1046/j.1365-294x.2000.00935.x. PMID 10849292.
  105. ^ Rhymer, Judith M.; Simberloff, Daniel (1996). "Extinction by Hybridization and Introgression". Annual Review of Ecology and Systematics. 27: 83–109. doi:10.1146/annurev.ecolsys.27.1.83.
  106. ^ Genetic Pollution from Farm Forestry using eucalypt species and hybrids; A report for the RIRDC/L&WA/FWPRDC]; Joint Venture Agroforestry Program; by Brad M. Potts, Robert C. Barbour, Andrew B. Hingston; September 2001; RIRDC Publication No 01/114; RIRDC Project No CPF – 3A; (PDF). Australian Government, Rural Industrial Research and Development Corporation. ISBN 978-0-642-58336-9. Archived from the original (PDF) on January 2, 2004. Retrieved April 22, 2017.
  107. ^ Bohling, Justin H.; Waits, Lisette P. (2015). "Factors influencing red wolf–coyote hybridization in eastern North Carolina, USA". Biological Conservation. 184: 108–116. doi:10.1016/j.biocon.2015.01.013.
  108. ^ Lanciotti, R. S.; Roehrig, J. T.; Deubel, V.; Smith, J.; Parker, M.; Steele, K.; Crise, B.; Volpe, K. E.; et al. (1999). "Origin of the West Nile virus responsible for an outbreak of encephalitis in the northeastern United States". Science. 286 (5448): 2333–2337. doi:10.1126/science.286.5448.2333. PMID 10600742. S2CID 34621778.
  109. ^ Hallegraeff, G.M. (1998). "Transport of toxic dinoflagellates via ships' ballast water: Bioeconomic risk assessment and efficacy of possible ballast water management strategies". Marine Ecology Progress Series. 168: 297–309. Bibcode:1998MEPS..168..297H. doi:10.3354/meps168297.
  110. ^ a b "Great Lakes Fishery Commission – Sea Lamprey". www.glfc.org. Retrieved October 24, 2017.
  111. ^ Simberloff, D. (2001). "Biological invasions – How are they affecting us, and what can we do about them?". Western North American Naturalist. 61 (3): 308–315. JSTOR 41717176.
  112. ^ 2008–2012 National Invasive Species Management Plan. Washington, DC.: National Invasive Species Council, Department of the Interior. 2008.
  113. ^ Holden, Matthew H.; Nyrop, Jan P.; Ellner, Stephen P. (June 1, 2016). "The economic benefit of time-varying surveillance effort for invasive species management". Journal of Applied Ecology. 53 (3): 712–721. doi:10.1111/1365-2664.12617.
  114. ^ "American serpentine leafminer – Liriomyza trifolii (Burgess)". entnemdept.ufl.edu. Retrieved November 20, 2019.
  115. ^ Eiswerth, M.E.; Darden, Tim D.; Johnson, Wayne S.; Agapoff, Jeanmarie; Harris, Thomas R. (2005). "Input-output modeling, outdoor recreation, and the economic impacts of weeds". Weed Science. 53: 130–137. doi:10.1614/WS-04-022R. S2CID 85608607.
  116. ^ Eurasian Watermilfoil in the Great Lakes Region. GreatLakes.net. Retrieved on September 1, 2007.
  117. ^ Sin, Hans; Radford, Adam (2007). "Coqui frog research and management efforts in Hawaii" (PDF). Managing Vertebrate Invasive Species: Proceedings of an International Symposium (G. W. Witmer, W. C. Pitt, K. A. Fagerstone, Eds). USDA/APHIS/WS, National Wildlife Research Center, Fort Collins, CO. Retrieved June 26, 2013.
  118. ^ a b c d Schlaepfer, Martin A.; Sax, DOV F.; Olden, Julian D. (2011). "The Potential Conservation Value of Non-Native Species". Conservation Biology. 25 (3): 428–437. doi:10.1111/j.1523-1739.2010.01646.x. PMID 21342267. S2CID 2947682.
  119. ^ Pelton, Tom (May 26, 2006) Baltimore Sun.
  120. ^ Zayed, Amro; Constantin, Șerban A.; Packer, Laurence (September 12, 2007). "Successful Biological Invasion despite a Severe Genetic Load". PLOS ONE. 2 (9): e868. Bibcode:2007PLoSO...2..868Z. doi:10.1371/journal.pone.0000868. PMC 1964518. PMID 17848999.
  121. ^ Adamson, Nancy Lee (2011). An Assessment of Non-Apis Bees as Fruit and Vegetable Crop Pollinators in Southwest Virginia. PhD Thesis. Virginia Polytechnic Institute and State University.
  122. ^ Wolverton, B. C.; McDonald, Rebecca C. (1981). "Energy from vascular plant wastewater treatment systems". Economic Botany. 35 (2): 224–232. doi:10.1007/BF02858689. S2CID 24217507.. Cited in Duke, J. (1983) Handbook of Energy Crops. Purdue University, Center for New Crops & Plants Products
  123. ^ Van Meerbeek, Koenraad; Appels, Lise; Dewil, Raf; Calmeyn, Annelies; Lemmens, Pieter; Muys, Bart; Hermy, Martin (May 1, 2015). "Biomass of invasive plant species as a potential feedstock for bioenergy production". Biofuels, Bioproducts and Biorefining. 9 (3): 273–282. doi:10.1002/bbb.1539.
  124. ^ Roelvink, Gerda; Martin, Kevin St; Gibson-Graham, J. K. (2015). Making Other Worlds Possible: Performing Diverse Economies. ISBN 978-0-8166-9329-0.
  125. ^ Holmes, Nick (March 27, 2019). "Globally important islands where eradicating invasive mammals will benefit highly threatened vertebrates". PLOS ONE. 14 (3): e0212128. Bibcode:2019PLoSO..1412128H. doi:10.1371/journal.pone.0212128. PMC 6436766. PMID 30917126.
  126. ^ de Wit, Luz A; Zilliacus, Kelly M; Quadri, Paulo; Will, David; Grima, Nelson; Spatz, Dena; Holmes, Nick; Tershy, Bernie; Howald, Gregg R; Croll, Donald A (2020). "Invasive vertebrate eradications on islands as a tool for implementing global Sustainable Development Goals". Environmental Conservation. 47 (3): 139–148. doi:10.1017/S0376892920000211. ISSN 0376-8929.
  127. ^ "Pursuing Sustainable Development for Island Communities by Removing Invasive Species". Island Conservation. August 13, 2020. Retrieved August 13, 2020.
  128. ^ Warren, Matt (May 8, 2018). "Rat begone: Record eradication effort rids sub-Antarctic island of invasive rodents". Science. Retrieved May 9, 2018.
  129. ^ Hester, Jessica Leight (May 17, 2018). "The Intrepid Rat-Sniffing Terriers of South Georgia Island". Atlas Obscura.
  130. ^ "Invasive plants can create positive ecological change". Science Daily. February 14, 2011. Invasive species could fill niches in degraded ecosystems and help restore native biodiversity....
  131. ^ Searcy, Christopher A.; Rollins, Hilary B.; Shaffer, H. Bradley (2016). "Ecological equivalency as a tool for endangered species management". Ecological Applications. 26 (1): 94–103. doi:10.1890/14-1674. PMID 27039512.
  132. ^ Hansen, Dennis M.; Donlan, C. Josh; Griffiths, Christine J.; Campbell, Karl J. (2010). "Ecological history and latent conservation potential: Large and giant tortoises as a model for taxon substitutions". Ecography: no. doi:10.1111/j.1600-0587.2010.06305.x.
  133. ^ a b Jacobsen, Rowan (March 24, 2014). "The Invasivore's Dilemma". Outside. Retrieved May 28, 2019.
  134. ^ Lai, Bun (September 1, 2013). "Invasive Species Menu of a World-Class Chef". Scientific American. 309 (3): 40–43. Bibcode:2013SciAm.309c..40L. doi:10.1038/scientificamerican0913-40. PMID 24003552.
  135. ^ Billock, Jennifer (February 9, 2016). "Bite Back Against Invasive Species at Your Next Meal". Smithsonian Magazine.
  136. ^ Snyder, Michael (May 19, 2017). "Can We Really Eat Invasive Species into Submission?". Scientific American.
  137. ^ Alien Entrées. The New Yorker (December 10, 2012). Retrieved on 2020-02-13.
  138. ^ Bio. Joeroman.com. Retrieved on February 13, 2020.
  139. ^ Eat The Invaders — Fighting Invasive Species, One Bite At A Time!. Eattheinvaders.org. Retrieved on February 13, 2020.
  140. ^ Bryce, Emma (February 6, 2015). "Cooking can't solve the threat of invasive species". The Guardian. Retrieved October 16, 2017.
  141. ^ Conniff, Richard (January 24, 2014). "Invasive Lionfish, the Kings of the Caribbean, May Have Met Their Match". Yahoo News. Archived from the original on January 27, 2014.
  142. ^ Parks, Mary and Thanh, Thai (2019). The Green Crab Cookbook. Green Crab R&d. ISBN 9780578427942.CS1 maint: multiple names: authors list (link)
  143. ^ "Lionfish Cookbook 2nd Edition | Reef Environmental Education Foundation".
  144. ^ a b c Lockwood, Julie L.; Hoopes, Martha F.; Marchetti, Michael P. (2007). Invasion Ecology (PDF). Blackwell Publishing. p. 7. Retrieved January 21, 2014.
  145. ^ a b c d Lowry, E; Rollinson, EJ; Laybourn, AJ; Scott, TE; Aiello-Lammens, ME; Gray, SM; Mickley, J; Gurevitch, J (2012). "Biological invasions: A field synopsis, systematic review, and database of the literature". Ecology and Evolution. 3 (1): 182–96. doi:10.1002/ece3.431. PMC 3568853. PMID 23404636.

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