- freely available
Forests 2012, 3(3), 840-852; doi:10.3390/f3030840
Published: 12 September 2012
Abstract: Invasive plant species have long been known to cause extensive damage, both economically and ecologically, to native ecosystems. They have historically been introduced by the public, both intentional and not, for a variety of reasons. Many of the woody shrubs, such as Lonicera maackii and Rosa multiflora were introduced for wildlife cover, forage, and ornamental value. These invasives have quickly out-competed native flora, in many cases drastically impacting and changing the environment they inhabit. In this review, chosen species characteristics have been described, their pathway to invasion explained, and their impacts to native wildlife highlighted. Based on a review of the scientific literature, we determined that not all effects by invasive plants are negative. Many positive impacts can be seen throughout the literature, such as native frogs utilizing Microstegium vimineum for cover and nesting habitat. However, some important invasive plant species were not included in this review due to a lack of literature on the subject of the effects on fauna. While much is known about their economic impact and the impact on native plant species, additional work needs to be done in the field of wildlife research to determine current impacts and future implications of non-native, invasive plants on native fauna.
The abundance of exotic, invasive plant species, hereafter invasive species, has increased dramatically in forested and other natural areas over the past few decades leading natural resource managers to become concerned about the future management in these areas. Invasive species can cause extensive environmental damage once they are established by altering ecosystem structure and function, which may lead to changes in nutrient cycling and decreased forest productivity in the invaded area [1,2]. In addition, invasive species often outcompete and replace native species decreasing native species biodiversity and, in some cases, lead to the extinction of endangered native plant species [3,4,5]. In the United States alone there are nearly 1000 plant species listed as either threatened or endangered, and of these, roughly 40% are considered at risk from invasive species due to direct contact, such as predation or indirect influences like competition . Control of invasive species can be costly, difficult, and time consuming. Billions of dollars have been spent in the United States over the past decade to prevent damage from invasive plants . Typically control of invasive species requires repeated treatments and long-term monitoring to ensure that the invasive species does not reestablish after treatment [1,8]. While research on the negative impacts of invasive plants on native flora diversity and production has been extensively documented [4,9,10,11], the effects of these invasive species on the native fauna are not as clear. Many invasive species are assumed to have negative consequences without sufficient research to back up these claims, simply for being out of their natural environment. For example, Lythrum salicaria (Purple loosestrife) was long considered to have large negative impacts to native bird populations [12,13], but once these reviews were looked at closely, it was revealed that this species had little to no negative impact on many of the native bird populations previously studied . We hypothesize that invasive species may have positive, as well as negative, impacts and that classifying invasive plants as either “good” or “bad” for a native ecosystem is missing the big picture. In this review, we will examine the current literature to determine the response of native fauna, both negative and positive, to some of the more common invasive plant species. The invasive species chosen, both woody and herbaceous, are highlighted in this review based on the current literature available on this subject and their spread throughout eastern North America. The sources used throughout this review were found through a systematic search of journals using keywords such as fauna, wildlife, effects, invasive species, etc. Though our expertise lies within eastern forests, the main points of this review are readily applicable to other woodland areas.
2. Woody Species
Many invasive shrubs were first introduced into North America for their aesthetic value, typically having bright berries or colorful flowers, or for providing wildlife habitat and forage [15,16]. For example, Rosa multiflora (multiflora rose), an invasive perennial shrub first introduced in the early 1900s, was used as “living fences” in landscaping, as it was less expensive than wire fences and to provide cover for wildlife . The species has spread throughout wooded areas and grasslands of eastern North America by seed that is dispersed by birds. Invasive woody species have many traits that have allowed them to be extremely successful in disturbed areas. Their growth is rapid, they are typically shade and drought tolerant, and are widely dispersed by seed-eating birds. These qualities have allowed these exotic species to out-compete native plant species and expand their ranges throughout the United Sates .
Lonicera maackii (Amur honeysuckle), a deciduous shrub from China that grows near riparian and forest edges, can reach heights of up to 6 m, leafs out before native species, and retains it leaves long after native species leaves have senesced. This species was originally brought to the United States in 1898 in hope to improve wildlife habitat with its high berry production . The species became established throughout the eastern North America where it thrives in urban or urban-fringe landscapes, particularly open sites and forest edges .
Research indicates twigs and foliage of L. maackii are consumed by small mammals and Odocoileus virginianus (white tailed deer) in eastern North America hardwood forests [18,19], while native songbirds readily consume the fleshy fruit produced . Meiners  reported that L. maackii also provides added cover for small mammals, but this can lead to increased seed predation and is a possible contributing factor to the decline in native tree seedlings. The presence of L. maackii has also been linked to an increase in mortality rates of songbird nests near watersheds, particularly in more urban landscapes [22,23]. Multiple theories have been proposed to explain this, one being that invasive shrubs tend to thrive on edges of forests and this leaves songbird nests within them more susceptible to predation [24,25,26]. Another hypothesis is that shrub height plays a factor and songbirds nests in invasive shrubs tend to be lower to the ground [27,28,29,30]. Some research has shown that nonindigenous shrubs may lack native plant defenses, such as thorns, which leave nests at a higher risk of predation . Amphibian populations may also be affected by the presence of L. maackii. In a laboratory study of amphibian populations native to oak dominated forest communities in the central United States, the Watling et al.  reported Anaxyrus americanus (American toad) mortality increased when tadpoles were raised in L. maackii extract compared to extract from native leaf litter. This increase was attributed to increased phenolic compounds that inhibited respiration. The other species studied Ambystoma maculatum (spotted salamander), Hyla sp. (tree frog), and Lithobates blairi (leopard frog) did not decrease in mortality when raised in L. maackii extract, but L. blairi behavior was altered in the extract which may make it more vulnerable to predators . Finally, research conducted by Allan et al.  has shown that with an increase in L. maackii, comes an increase in ticks and tick-borne diseases. In this study, O. virgianus preferred habitat with a higher density of invasive shrub and being a common host for ticks, where more O. virgianus were found so were more ticks and tick-borne diseases. Obvious implications for this can be an increase in human exposures to the diseases and an expansion of the infected tick population .
Berberis thunbergii (Japanese Barberry) is an invasive, compact, thorny perennial shrub that is native to southern and central Japan . Berberis thunbergii was originally introduced to the New England area around 1875 for ornamental value, wildlife, and erosion control . It now has established populations throughout the northeastern United States, as well as five provinces in Canada. Berberis thunbergii grows best in well-drained soils and prefers areas with partial sunlight, making edges, roadsides, fences, and old fields ideal environments, but the species can flower and produce seed under full shade .
Work conducted in southeastern New York has shown that this invasive shrub may have some positive effects on avain abundance in woodland communities. Schmidt et al.  reported that nesting success of Catharus fuscescens (veeries) built in B. thunbergii were less likely to be predated upon than those nests located on the ground, had twice the fledgling success as ground nests, and were overall chosen at a higher rate than other substrates. This was attributed to less rodent predation, due to rodents seeming to avoid foraging near B. thunbergii . Work done in Connecticut suggests areas infested with B. thunbergii provide ideal habitat for small mammals and O. virginianus, however this may also increase tick populations . Peromyscus leucopus (white-footed mouse) is a common host for ticks. With an increase in P. leucopus populations, came an increase in Ixodes scapularis (blacklegged ticks). Finally, although B. thunbergii is generally considered browse resistant, O. virginianus has been observed consuming B. thunbergii berries when other forage was scarce [34,36].
Elaeagnus umbellata (Autumn Olive), an invasive shrub native to Asia, was brought to the United States for wildlife usage . Until recently it was recommended as a cover crop to improve wildlife habitat . However, it was recognized as a problematic species that reduces native plant species diversity and productivity and is now considered invasive . Elaeagnus umbellata can be found throughout the eastern United States in woodlands, grasslands, abandoned fields, and other disturbed areas. It is drought and moderately shade tolerant, enabling it to survive on a variety of sites.
As mentioned, E. umbellata was introduced for wildlife purposes therefore it is no surprise that multiple bird species utilize this invasive shrub for both cover and nesting sites . Native bird species also readily consume the fruit produced including Bonasa umbellus (ruffed grouse), Colinus virginianus (northern bobwhite), Zenaida macroaura (mourning dove), Cardinalis cardinalis (northern cardinal), Passerella iliaca (fox sparrow), and Melospiza melodia (song sparrow) . In a study of feeding choices between fruit from native species and E. umbellata fruit, Turdus migratorius (American robin) preferred the invasive species fruit . However, widespread consumption of E. umbellata fruit, as well as other invasive plant fruit, has facilitated the spread of invasive species in hardwood forests in the eastern United States [42,43]. Although it can be browsed by O. virginianus, Knapp et al.  reported that preference for native species by the large herbivore can also facilitate invasion of E. umbellata. This is an example of the enemy release hypothesis that has become such a staple among researchers in the field of invasive species. When these species move from their native habitat to a foreign area, they are generally faced with little or no natural predators, allowing for an unchecked growth. The ecological implications of this can be great. While invasive species go without predation, native species are preferentially consumed and allow for an even greater expansion of the non-native species. These implications should be considered when developing management plans.
3. Herbaceous Species
Although not as common as invasive woody species in forested areas , invasive herbaceous species can be problematic in areas they invade. While invasive herbaceous species typically require some disturbance before the population invades into forested areas, some species such as Alliara petiolata (garlic mustard) can invade mature forests and outcompete native plants . As observed with some invasive woody plant species, some invasive herbaceous plant species have been able to out-compete native species in eastern hardwood forests due to the selective foraging of the large populations of O. virginianus . As O. virginianus preferentially browse native plants, while avoiding non-native plant species, the invasive plants are given the opportunity to reproduce and spread without barriers.
Alliara petiolata (Garlic mustard) is a cool season, biennial herb native to western Eurasia. It is believed to first be introduced into America by early settlers using it as a culinary herb as well as for medicinal properties [48,49]. In its native range, it is generally found in humid maritime climates with high shade. Its current range in North America is from southern Ontario down through Tennessee and throughout New England and the Midwest. The species ranges in height from 30 to 100 cm and invades the ground cover of disturbed and undisturbed forested areas, preferring moist and shaded areas near rivers, floodplains and edges .
There have been no published reports highlighting the positive impacts of A. petiolata on forest fauna; however several examples of negative impacts exist in the literature. Presence of A. petiolata was attributed to decreased population decline of Pieris napioleracea (mustard white butterfly) a rare, native butterfly found in the northeastern United States . The authors reported that although females would oviposit on A. petiolata plants, the plant did not support larval growth, thus decreasing population persistence. Other research suggests that A. petiolata is unpalatable to O. virginianus, which facilitates the invasive success of the plant in eastern North American forests . Knight et al.  observed O. virginianus preferential browsing on native forest plants such as Trillium grandiflorum (white trillium), Asarum canadense (wild ginger), Polygonatum biflorum (Solomon’s seal), Arisaema truphyllum (Jack-in-the-pulpit), Sanguinaria canadensis (bloodroot) and Hydrophyllum virginianum (Virginia waterleaf) in a Pennsylvania hardwood forests. The authors concluded that as O. virginianus preferentially chose native herbaceous species over non-native. With no natural predators to consume the non-native species the understory of this forest quickly turned to a highly invasive composition, completely changing the habitat for other native fauna .
Lythrum salicaria (Purple loosestrife) is a fast growing Eurasian perennial herb associated with wetland, marshy, or riparian sites . Height ranges from 0.5 to 3.5 m . It was first introduced to the United States in the 1800s as an ornamental  and quickly spread through marshes and wetlands dispersed primarily by water, but also assisted by waterfowl and other birds . This invasive species is extremely hard to eradicate due to its massive seed bank, up to ten times larger than any other wetland species, and the fact that seeds can remain dormant in the soil for years .
Although initial reviews (e.g., [12,13]) indicated dense stands of L. salicaria create conditions which negatively impact wildlife, much of the evidence used to support this argument was anecdotal and unsubstantiated by peer reviewed studies and the impact of L. salicaria on wildlife populations is not as negative as once believed . In a study of avian responses to areas invaded by L. salicaria Whitt et al.  reported a negative impact on Cistothorus palustris (marsh wren), but five other bird species observed were not affected by L. salicaria. There is evidence that compounds leached from L. salicaria significantly reduce survival rates and overall performance of Bufo americanus (American toad tadpoles) , but rates used in the experiment were greater than what is naturally found in the environment . In an extensive review on the impacts of L. salicaria, Lovoie  reported that there have been no studies published on small mammals or waterfowl making it difficult for critical analysis on the impact of this species on wildlife populations in the eastern North America.
Microstegium vimineum (Japanese stiltgrass), an annual, C4 grass species native to southeastern Asia, first appeared in the United states in Tennessee in 1919, but has spread throughout most of the United States east of the Mississippi [10,59,60,61]. It can grow in a wide variety of soil and light conditions forming dense monocultures on the forest floors . Microstegium viminuem produces an abundant amount of seed that remains viable in the seed bank for a number of years after production making it a difficult species to control. It typically invades streamside forest habitat and is spread through animal or water dispersal, preferably in disturbed areas .
Originally introduced to the North America as packing material, M. vimineum is unpalatable to most forest herbivores, including generalist species such as O. virginianus showing again how an invasive species may overtake a habitat due to exclusion from browsing, In areas where large populations of O. virginianus and M. vimineum exist, the herbivore prefers to browse other native grasses , reducing native plant species and in turn increasing M. vimineum populations [51,65]. In a study of invasive plant ecology in southern Appalachia, Webster et al.  reported heavy foraging by O. virginianus reduced the ability of native plant species to recover during times of drought, when M. vimineum is susceptible of being overtopped, resulting in continued dominance of M. vimineum. However, in areas where high O. virginianus populations have decreased native understory plant species abundance, such as urbanized forest, M. vimineum may have some positive impacts on forest fauna. Nagy et al.  reported areas invaded with M. vimineum provided cover for native frogs in old growth Tsuga canadensis (eastern hemlock) and secondary hardwood dominated forests in New York. Amphibians utilized stands of M. vimineum when O. virginianus browsing has reduced native cover . Increased frog abundance was attributed increased moisture retention in of areas invaded with M. vimineum as well as extra food due to the increase abundance of earthworms in highly invaded areas .
Phalaris arundinacea (Reed Canary Grass) is a cool season, large coarse perennial grass that can reach heights of up to 2 m and reproduces through seeds or rhizomes . There grass is native to North American and Eurasian. The Eurasian varieties were introduced as early as the 1800s for soil control, and though they are very difficult to tell apart it, is generally thought that the Eurasian type is the invasive species due to its increased aggressiveness compared to its native counterpart . Phalaria arundinacea grows best on wet, fertile soils in full sun. It is very aggressive in riparian forest areas, and can particularly be a problem in young forest stands. The species forms dense monotypic stands that decrease native plant species diversity and productivity .
Reviews of P. arundinacea suggest that although the species is palatable to livestock and wildlife, it is not superior to other forage grasses [69,70]. However, multiple studies indicate that the species provides cover for a number of small mammal, large ungulate species and upland game birds , and nesting habitat for Rana pipiens (northern leopard frog) . In a statewide study of bottomland areas invaded by P. arundinacea in Illinois, Spryreas et al.  reported that although increased abundance of P. arundinacea corresponded with a decrease in native plant cover and diversity, changes in faunal abundance were not as clear. Some groups of fauna, such as homopterans and Peromyscus leucopus (white-footed mouse), showed a negative correlation in regards to diversity and abundance. However, species abundance for Microtus spp. (voles) increased with P. arundinacea cover. Finally, many more groups of fauna including avian, other small mammals, and arthropod communities showed no correlation either way.
This review highlights the impact of invasive plants on fauna in eastern North American ecosystems. While invasive plants are generally reported to have negative impacts on ecosystem function and diversity [1,2], our review indicates that they can also have many positive impacts on fauna in eastern ecosystems, particularly in ecosystems near developed areas that are otherwise devoid of plant cover (Table 1). The positive impact of invasive plants on forest fauna should not come as a surprise, as many of these species were introduced to benefit wildlife as a food source or for cover [15,34,37]. However, in comparison to studies of invasive plants on productivity and diversity, we observed that studies examining of the impact on forest fauna were somewhat limited in the scientific literature. For example, several problematic invasive plants in the southeastern United States such as Imperata cylindrica (cogongrass) and Pueraria montana var. lobata (kudzu) were not discussed in this paper because of the paucity of information available on the impact of these species on forest fauna. In addition, this review primarily focused on the direct impacts of invasive plant species on forest fauna, we did not examine the indirect impacts, such as, the consequences of an invasive plant species reducing native tree regeneration and potentially changing future forest cover. Therefore we feel that the impact of invasive plant species is variable and think that it is not prudent to group all invasive plants together as “good” or “bad” for forest fauna in eastern North America. This idea has become a large area for debate in the ecological community. In 2011, Davis et al.  published a paper claiming that the main reason for our attempts at controlling invasive species is due to tradition and a bias within ecological and conservation societies. They bring to light the ideas that many of the species considered today to be native were once non-native and that many native species cause much more damage than their non-native counterparts. One example being Dendroctonus ponderosae, the mountain pine beetle, which has had negative effects to the ecosystems it has been expanding to but has not been dealt with like other invasive beetle species. Finally, they discuss the idea that the manpower and cost for attempting to control invasive species is too high for the benefits to outweigh them . Another thought to consider is that many invasive plant species are found in areas where native species have been removed because of development. For instance, L. maackii prefers disturbed urban areas where other shrubs may not be found. Many of the species mentioned in this review thrive in disturbed areas with less light, water, and nutrient availability, which raises the question: is some ground cover, even invasive, better for native wildlife than none? Judgment should be made for individual species (plant and fauna) for a given ecosystem before determining what management action should be made for (or against) that species.
|Table 1. Summary of negative and positive effects of invasive plant species on native fauna in eastern North America.|
|Invasive Plant Species||Negative Effects||Positive Effects||References|
|Rosa multiflora||Provide cover for wildlife|||
|Lonicera maackii||Increase mortality of songbird nests||Provides cover for small seed-eating mammals||[12,15,16,17,18,19,20,28]|
|Increase in tadpole mortality rate|
|Provides forage in form of berries, twigs, and foliage|
|Berberis thunbergii||Certain rodents avoid||Decrease songbird nest predation||[30,31,32,36,37]|
|Increase in black-legged tick population||Increase white-footed mice populations|
|Provide forage for O. virginianus when other sources are scarce|
|Elaeagnus umbellata||Preferred nesting areas for certain songbirds|
|Provides cover and food for songbirds|
|Alliara petiolata||O. virginianus do not use as forage||[43,46,47]|
|Decline in population of P. napi oleracea|
|Lythrum salicaria||Possible negative effects to C. palustris||[56,57]|
|Reduce survival rates of American Toad tadpoles|
|Microstegium viminuem||Unpalatable to most forest herbivores||Provides cover for native frog populations||[63,65]|
|Retains moisture, utilized by amphibians|
|Phalaris arundinacea||Decrease in homopteran diversity and abundance||Cover for a variety of wildlife||[69,70,71]|
|Nesting habitat for R. pipiens|
|Decrease P. leucopus populations||Increase populations of Microtus spp.|
Conflict of Interest
The authors declare no conflict of interest.
- Webster, C.R.; Jenkins, M.A.; Jose, S. Woody invaders and the challenges they pose to forest ecosystems in the Eastern United States. J. For. 2006, 104, 366–374. [Google Scholar]
- Holzmueller, E.J.; Jose, S. Invasion success of cogongrass, an alien C4 perrennial grass, in the southeastern United States: Exploration of the ecological basis. Biol. Invasions 2010, 13, 435–442. [Google Scholar] [CrossRef]
- Schmitz, D.C.; Simberloff, D. Biological invasions: A growing threat. Issues Sci. Technol. 1997, 13, 33–40. [Google Scholar]
- Wilcove, D.S.; Rothstein, D.; Dubow, J.; Phillips, A.; Losos, E. Quantifying threats to imperiled species in the United States. BioScience 1998, 48, 607–615. [Google Scholar] [CrossRef]
- Gaertner, M.; Den Breeyen, A.; Hui, C.; Richardson, D.M. Impacts of alien plant invasions on species richness in Mediterranean-type ecosystems: A meta-analysis. Prog. Phys. Geogr. 2009, 33, 319–338. [Google Scholar] [CrossRef]
- Pimentel, D.; Lach, L.; Zuniga, R.; Morrison, D. Environmental and economic costs of nonindigenous species in the United States. BioScience 2000, 50, 53–65. [Google Scholar] [CrossRef]
- Pimental, D.; Zuniga, R.; Morrison, D. Update on the environmental and economic costs associated with alien-invasive species in the United States. Ecol. Econ. 2005, 52, 273–288. [Google Scholar] [CrossRef]
- Jose, S.; Cox, J.; Miller, D.L.; Shilling, D.G.; Merritt, S. Alien plant invasions: The story of cohongrass in southeastern Florida. J. For. 2002, 100, 41–44. [Google Scholar]
- Mack, R.N.; Simberloff, D.; Lonsdale, W.M.; Evans, H.; Clout, M.; Bazzaz, F.A. Biotic invasions: Causes, epidemiology, global consequences, and control. Ecol. Appl. 2000, 10, 689–710. [Google Scholar] [CrossRef]
- Ehrenfeld, J.G. A rhizomatous, perennial form of Microstegium vimineum (Trin.) A. Camus in New Jersey. J. Torrey Bot. Soc. 1999, 126, 352–358. [Google Scholar] [CrossRef]
- Holzmueller, E.J; Jose, S. Invasive plant conundrum: What makes aliens so successful? J. Trop. Agric. 2009, 47, 18–29. [Google Scholar]
- Thompson, D.Q.; Stuckey, R.L.; Thompson, E.B. Spread, Impact, and Control of Purple Loosestrife (Lythrum salicaria) in North American Wetlands; U.S. Department of Agriculture, Fish and Wildlife Service: Washington, DC, USA, 1987; p. 55. [Google Scholar]
- Blossey, B. Before, during, and after: The need for long-term monitoring in invasive plant species management. Biol. Invasions 1999, 1, 301–311. [Google Scholar] [CrossRef]
- Lavoie, C. Should we care about purple loosestrife? The history of an invasiveplant in North America. Biol. Invasions 2010, 12, 1967–1999. [Google Scholar] [CrossRef]
- Luken, J.O.; Thieret, J.W. Honeysuckle, its fall from grace. BioScience 1996, 46, 18–24. [Google Scholar] [CrossRef]
- Vermeire, L.T.; Bidwell, T.G.; Stritzke, J. Ecology and Management of Sericea Lespedeza. OSU Extension Facts F-2874; Oklahoma Cooperative Extension Service: Stillwater, OK, USA, 2005. [Google Scholar]
- Edwards, G. Wild and Old Garden Roses; Hafner Press: New York, NY, USA, 1975. [Google Scholar]
- Vellend, M. A pest and an invader: White-tailed deer (Odocoileus virginianus Zimm.) as a seed dispersal agent for honeysuckle shrubs (Lonicera L.). Nat. Areas J. 2002, 22, 230–234. [Google Scholar]
- Meiners, S.J. Apparent competition: An impact of exotic shrub invasion on tree regeneration. Biol. Invasions 2007, 9, 849–855. [Google Scholar] [CrossRef]
- Williams, C.E.; Ralley, J.J.; Taylor, D.H. Consumption of seeds of the invasive amur honeysuckle Lonicera maackii Rupr. Maxim. by small mammals. Nat. Areas J. 1992, 12, 86–89. [Google Scholar]
- Bartuszevige, A.M.; Gorchov, D.L. Avian seed dispersal of an invasive shrub. Biol. Invasions 2006, 8, 1013–1022. [Google Scholar] [CrossRef]
- Borgmann, K.L.; Rodewald, A.D. Nest predation in an urbanizing landscape: The role of exotic shrubs. Ecol. Appl. 2004, 14, 1757–1765. [Google Scholar] [CrossRef]
- Schmidt, K.A.; Whelan, C.J. Effects of exotic Lonicera and Rhamnus on songbird nest predation. Conserv. Biol. 1999, 13, 1502–1506. [Google Scholar] [CrossRef]
- Gates, J.E.; Gysel, L.W. Avian nest dispersion and fledging success in field-forest ecotones. Ecology 1978, 59, 871–883. [Google Scholar] [CrossRef]
- Paton, P.W.C. The effect of edge on avian nest success: How strong is the evidence? Conserv. Biol. 1994, 8, 17–26. [Google Scholar]
- King, D.I.; Griffin, C.R.; de Graaf, R.M. Effects of clearcutting on habitat use and reproductive success of the ovenbird in forested landscapes. Conserv. Biol. 1996, 10, 1380–1386. [Google Scholar]
- Best, L.B.; Stauffer, D.E. Factors affecting nesting success in riparian bird communities. Condor 1980, 82, 149–158. [Google Scholar] [CrossRef]
- Filliater, T.S.; Breitwisch, R.; Nealen, P.M. Pre-dation on Northern Cardinal nests: Does choice of nest site matter? Condor 1994, 96, 761–768. [Google Scholar] [CrossRef]
- Allan, B.F.; Dutra, H.P.; Goessling, L.S.; Barnett, K.; Chase, J.M.; Marquis, R.J.; Pang, G.; Storch, G.A.; Thach, R.E.; Orrock, J.L. Invasive honeysuckle eradication reduces tick-borne disease risk by altering host dynamics. Proc. Natl. Acad. Sci. USA 2010, 107, 18523–18527. [Google Scholar]
- Martin, T.E. Processes organizing open-nesting bird assemblages: Competition or nest predation? Evol. Ecol. 1988, 2, 37–50. [Google Scholar] [CrossRef]
- Martin, T.E. Nest predation and nest sites: New per-spectives on old patterns. BioScience 1993, 43, 523–532. [Google Scholar] [CrossRef]
- Watling, J.I.; Hickman, C.R.; Lee, E.; Wang, K.; Orrock, J.L. Extracts of the invasive shrub Lonicera maackii increase mortality and alter behavior of amphibian larvae. Oecologia 2011, 165, 153–159. [Google Scholar] [CrossRef]
- Ohwi, J. Flora of Japan; Smithsonian Institution: Washington, DC, USA, 1965. [Google Scholar]
- Silander, J.A.; Klepeis, D.M. The invasion ecology of Japanese Barberry (Berberis thunbergii) in the New England landscape. Biol. Invasions 1999, 1, 189–201. [Google Scholar] [CrossRef]
- Schmidt, K.A.; Nelis, L.C.; Briggs, N.; Ostfeld, R.S. Invasive shrubs and songbird nesting success: Effects of climate variability and predator abundance. Ecol. Appl. 2005, 15, 258–265. [Google Scholar] [CrossRef]
- Williams, S.C.; Ward, J.S.; Worthley, T.E.; Stafford, K.C., III. Managing Japanese Barberry (Ranunculales: Berberidaceae) infestations reduces Blacklegged Tick (Acari: Ixodidae) abundance and infection prevalence with Borrelia burgdorferi (Spirochaetales: Spirochaetaceae). Environ. Entomol. 2009, 38, 977–984. [Google Scholar] [CrossRef]
- Allan, P.F.; Steiner, W.W. Autumn Olive for Wildlife and Other Conservation Uses, Leaflet No. 458; U.S. Department of Agriculture: Washington, DC, USA, 1965; p. 8. [Google Scholar]
- Henry, J. A bonanza for wildlife. Soil Conserv. 1980, 45, 13. [Google Scholar]
- Ebinger, J.E. Exotic shrubs: A potential problem in natural area management in Illinois. Nat. Areas J. 1983, 3, 3–6. [Google Scholar]
- De Graaf, R.M. Trees, Shrubs, and Vines for Attracting Birds; University Press of New England: Lebanon, NH, USA, 2002; pp. 87–88. [Google Scholar]
- Lafleur, N.E.; Rubega, M.A.; Elphick, C.S. Invasive fruits, novel foods, and choice: An investigation of European starling and American Robin frugivory. Wilson J. Ornithol. 2007, 119, 429–438. [Google Scholar] [CrossRef]
- White, D.W.; Stiles, E.W. Bird dispersal of fruits of species introduced into eastern North America. Can. J. Bot. 1992, 70, 1689–1696. [Google Scholar] [CrossRef]
- McCay, T.S.; McCay, D.H.; Czajka, J.L. Deposition of exotic bird-dispersed seeds into three habitats of a fragmented landscape in the northeastern United States. Plant Ecol. 2009, 203, 59–67. [Google Scholar] [CrossRef]
- Knapp, L.B.; Fownes, J.H.; Harrington, R.A. Variable effects of large mammal herbivory on three non-native versus three native woody plants. For. Ecol. Manag. 2008, 255, 92–98. [Google Scholar] [CrossRef]
- Lowe, S.; Browne, M.; Boudjelas, S.; de Poorter, M. 100 of the World’s Worst Invasive Alien Species A selection from the Global Invasive Species Database; The Invasive Species Specialist Group (ISSG), a specialist group of the Species Survival Commission (SSC) of the World Conservation Union (IUCN): Auckland, New Zealand, 2004; p. 12. [Google Scholar]
- McCarthy, B.C. Response of a Forest Understory Community to Experimental Removal of an Invasive Nonindigenous Plant (Alliaria Petiolata, Brassicaceae). In Assessment and Management of Plant Invasions; Luken, J.O., Thieret, J.W., Eds.; Springer: New York, NY, USA, 1997; pp. 117–130. [Google Scholar]
- Knight, T.M.; Dunn, J.L.; Smith, L.A.; Davis, J.; Kalisz, S. Deer facilitate invasive plant success in a Pennsylvania forest understory. Nat. Areas J. 2009, 29, 110–116. [Google Scholar] [CrossRef]
- Welk, E.; Schubert, K.; Hoffman, M.H. Present and potential distribution of invasive garlic mustard (Alliaria petiolata) in North America. Divers. Distrib. 2002, 8, 219–233. [Google Scholar] [CrossRef]
- Blossey, B.; Nuzzo, V.; Hinz, H.; Gerber, E. Developing biological control of Alliara petiolata (M. Bieb.) Cavara and Grande (Garlic Mustard). Nat. Areas J. 2001, 21/4, 357–367. [Google Scholar]
- Keeler, M.S.; Chew, F.S.; Goodale, B.C.; Reed, J.M. Modeling the impacts of two exotic invasive species on a native butterfly: Top-down vs. bottom-up effects. J. Anim. Ecol. 2006, 75, 777–788. [Google Scholar] [CrossRef]
- Eschtruth, A.K.; Battles, J.J. Acceleration of exotic plant invasion in a forested ecosystem by a generalist herbivore. Conserv. Biol. 2009, 23, 388–399. [Google Scholar] [CrossRef]
- Mullen, B.H. The biology and management of Purple Loosestrife (Lythrum salicaria). Weed Technol. 1998, 12, 397–401. [Google Scholar]
- Mal, T.K.; Lovett-Doust, J.; Lovett-Doust, L.; Mulligan, G.A. The biology of Canadian weed. 100. Lythrum salicaria. L. in Manitoba. Hortscience 1992, 28, 954. [Google Scholar]
- Stuckey, R.L. Distributional history of Lythrum salicaria (Purple loosestrife) in North America. Bartonia 1980, 47, 3–20. [Google Scholar]
- Balogh, G.R. Distribution and seedling ecology of purple loosestrife Lythrum-salicaria in Ohio’s Lake Erie marshes USA. Ohio J. Sci. 1986, 89, 62–64. [Google Scholar]
- Welling, C.H.; Becker, R.L. Life History and Taxonomic Status of Purple Loosestrife in Minnesota: Implications for Management and Regulation of this Exotic Plant; Minnesota Department of Natural Resources: Little Falls, MN, USA, 1992; Volume 146, pp. 1–15. [Google Scholar]
- Whitt, M.B.; Prince, H.H.; Cox, R.R., Jr. Avian use of Purple loosestrife dominated habitat relative to other vegetation types in a Lake Huron wetland complex. Wilson Bull. 1999, 111, 105–114. [Google Scholar]
- Maerz, J.C.; Brown, C.J.; Chapin, C.T.; Blossey, B. Can secondary compounds of an invasive plant affect larval amphibians? Funct. Ecol. 2005, 19, 970–975. [Google Scholar] [CrossRef]
- Fairbrothers, D.E.; Gray, J.R. Microstegium vimineum (Trin.) A. Camus (Gramineae) in the United States. Bull. Torrey Bot. Club. 1972, 99, 97–100. [Google Scholar] [CrossRef]
- Hunt, D.; Zaremba, R. The northeastern spread of Microstegium vimineum (Poaceae) into New York and adjacent states. Rhodora 1992, 94, 167–170. [Google Scholar]
- Redman, D.E. Distribution and habitat types for Nepal Microstegium (Microstegium vimineum (Trin.) Camus) in Maryland and the District of Co-lumbia. Castanea 1995, 60, 270–275. [Google Scholar]
- Cole, P.G.; Weltzin, J.F. Environmental correlates of the distribution and abundance of Microstegium vimineum, in East Tennessee. Southeast. Nat. 2004, 3, 545–562. [Google Scholar] [CrossRef]
- Gibson, D.J.; Spyeareas, G.; Benedict, J. Life history of Microstegium vimineum (Poaceae), an invasive grass in southern Illinois. J. Torrey Bot. Soc. 2002, 129, 207–219. [Google Scholar] [CrossRef]
- Miller, J.H.; Miller, K.V. Forest Plants of the Southeast and their Wildlife Uses; Southern Weed Science Society: Auburn, AL, USA, 1999. [Google Scholar]
- Baiser, B.; Lockwood, J.L.; La Puma, D.; Aronson, M.F.J. A perfect storm: Two ecosystem engineers interact to degrade deciduous forests of New Jersey. Biol. Invasions 2008, 10, 785–795. [Google Scholar] [CrossRef]
- Nagy, C.; Aschen, S.; Christie, R.; Weckel, M. Japanese stilit grass (Microstegium vimineum),a nonnative invasive grass, provides alternative habitat for native frogs in a suburban forest. Urban Habitats Online J. 2001, 6. Available online: http://www.urbanhabitats.org/v06n01/ (accessed on 15 June 2012). [Google Scholar]
- Carlson, I.T.; Oram, R.N.; Surprenant, J. Reed canarygrass and other Phalaris species. Agron. Monogr. 1996, 34, 569–604. [Google Scholar]
- Lavergne, S.; Molofsky, J. Reed canary grass (Phalaris arundinacea) as a biological model in the study of plant invasions. Crit. Rev. Plant Sci. 2004, 23, 415–429. [Google Scholar] [CrossRef]
- Martin, A.C.; Zim, H.S.; Nelson, A.L. American Wildlife and Plants; McGraw-Hill Book Company: New York, NY, USA, 1951; p. 500. [Google Scholar]
- Waggy, M.A. Phalaris Arundinacea. Fire Effects Information System; U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory: Fort Collins, CO, USA, 2010. Available online: http://www.fs.fed.us/database/feis/ (accessed on 15 June 2012). [Google Scholar]
- Gilbert, M.; Leclair, R., Jr.; Fortin, R. Reproduction of the northern leopard frog (Rana pipiens) in floodplain habitat in the Richelieu River, P. Quebec, Canada. J. Herpetol. 1994, 28, 465–470. [Google Scholar] [CrossRef]
- Spyreas, G.; Wilm, B.W.; Plocher, A.E.; Ketzner, D.M.; Matthews, J.W.; Ellis, J.L.; Heske, E.J. Biological consequences of invasion by reed canary grass (Phalaris arundinacea). Biol. Invasions 2010, 12, 1253–1267. [Google Scholar] [CrossRef]
- Davis, M.A.; Chew, M.K.; Hobbs, R.J.; Lugo, A.E.; Ewel, J.J.; Vermeij, G.J.; Brown, J.H.; Rosenzweig, M.R.; Gardener, M.R.; Carroll, S.P.; et al. Don’t judge species on their origins. Nature 2011, 474, 153–154. [Google Scholar]
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