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Invasion by Non-Native Riparian Plants Negatively Impacts Terrestrial Invertebrates

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Invasion by Non-Native Riparian Plants Negatively Impacts Terrestrial Invertebrates View metadata, citation and similar papers at core.ac.uk brought to you by CORE provided by Stirling Online Research Repository Biol Invasions https://doi.org/10.1007/s10530-019-01947-5 (0123456789().,-volV)( 0123456789().,-volV) ORIGINAL PAPER All change at the water’s edge: invasion by non-native riparian plants negatively impacts terrestrial invertebrates Alex Seeney . Sophie Eastwood . Zarah Pattison . Nigel J. Willby . Colin D. Bull Received: 26 June 2018 / Accepted: 16 February 2019 Ó The Author(s) 2019 Abstract Riparian zones are complex, dynamic with increasing cover, but this was not observed for F. habitats that play a critical role in river ecosystem japonica. INNP affected terrestrial invertebrate mor- functioning. Terrestrial invertebrates comprise much phospecies abundance and diversity, to a greater of the diversity found in riparian habitats and facilitate extent than prevailing environmental conditions. Our the transfer of energy between aquatic and terrestrial findings therefore offer support for managing riparian systems. However, the consequences for terrestrial plant invasions to improve habitat heterogeneity, invertebrates of invasion of riparian zones by invasive restore terrestrial invertebrate diversity and repair non-native plants (INNP) remain poorly understood. aquatic-terrestrial linkages. Responses of terrestrial macroinvertebrate morphos- pecies to invasion by two common INNP, Fallopia Keywords Diversity Á Fallopia japonica Á Impatiens japonica (Japanese knotweed) and Impatiens glan- glandulifera Á Invasive species Á Morphospecies dulifera (Himalayan balsam) were assessed, relative to local environmental factors. Terrestrial invertebrates were collected from 20 sites on low order streams in June and August alongside data on physical attributes Introduction and land use. Greater cover of F. japonica and I. glandulifera cover reduced total invertebrate abun- Terrestrial invasive non-native plants (INNP) repre- dance and morphospecies diversity at the individual sent over 300 of the established plant species in sample scale, whilst increasing spatial heterogeneity Europe (Keller et al. 2011). INNP are often associated of invertebrates at the site scale. Impatiens glandulif- with reductions in overall biodiversity (Barney et al. era reduced morphospecies diversity at the site scale 2015), lower abundance of terrestrial primary con- sumers (McCary et al. 2016) and disruption of above and below-ground fungal communities (Pattison et al. Electronic supplementary material The online version of 2016). Negative impacts on ecosystem services such this article (https://doi.org/10.1007/s10530-019-01947-5) con- as pollination and biomass production may also be tains supplementary material, which is available to authorized users. associated with INNP (Hulme et al. 2013), alongside altered rates of erosion and water use compared to A. Seeney (&) Á S. Eastwood Á Z. Pattison Á their native counterparts (Pejchar and Mooney 2009). N. J. Willby Á C. D. Bull Impacts on ecosystem services and biodiversity com- Biological and Environmental Sciences, University of Stirling, Stirling FK9 4LA, UK prise some of the main criteria for listing a species as e-mail: [email protected] 123 A. Seeney et al. an invasive alien species (IAS) under EU regulation ecosystems they invade (Ehrenfeld 2010). Gerber No. 1143/2014, which covers the prevention, man- et al. (2008) demonstrated that riparian habitats agement and spread of IAS (European Union 2014). invaded by Fallopia species harboured a reduced INNP are also responsible for societal and economic abundance and morphospecies richness of terrestrial losses, particularly when they colonise and disrupt invertebrates, whilst Ruckli et al. (2013) showed that I. agricultural land (Duncan et al. 2004), and often glandulifera supported a higher abundance and require costly investment to manage and/or repair species richness of gastropods compared to uninvaded ecological damage (such as flood damage following plots. A range of responses by flower-visiting insect INNP colonisation) (Zavaleta 2000). Societal reac- communities at sites colonised by INNP were demon- tions to IAS may also depend on visible effects of strated by Davis et al. (2018), including higher insect visible invaders (Simberloff et al. 2013), which may diversity associated with I. glandulifera and lower hinder restoration efforts following colonisations by abundance of solitary bees and hoverflies associated less prominent IAS. with Heracleum mantegazzianum (giant hogweed). The case for managing INNP is often built on Riparian zones support a disproportionately high evidence of their impacts, but such evidence can prove species diversity (Gerber et al. 2008) and thus offer contentious. Conflicting arguments highlight potential suitable habitats for studying the effects of INNP on benefits of INNP, such as use of Impatiens glandulif- invertebrate communities, especially as the structural era (Himalayan balsam) by pollinators (Bartomeus complexity afforded by plant communities is an et al. 2010), or use of INNP biomass as feed for important mediator of predator–prey dynamics (Grut- livestock (Van Meerbeek et al. 2015), but also invoke ters et al. 2015). Fallopia japonica (Japanese knot- detrimental legacy effects of INNP introductions weed) and I. glandulifera are two of the INNP species (Iacarella et al. 2015; Corbin and D’Antonio 2017). most commonly associated with riparian habitats in Naturally dynamic systems are particularly prone to the northern hemisphere, the former being listed invasion by non-native species (Catford et al. 2012); among the world’s 100 worst invasive alien species riparian habitats, characterised by fluvial disturbance (Lowe et al. 2000). Impatiens glandulifera was first and exposed to waterborne transport of propagules, are introduced from the Himalayas in the early 1800s thus amenable to invasions (Lawson et al. 2015). (Perrins et al. 1993), and has subsequently become one However, little is known about how invasion of of the most widespread invasive plants in the UK riparian habitats by INNP impacts their terrestrial (Pattison et al. 2016) due to its ability to thrive in invertebrate communities. disturbed environments (Greenwood and Kuhn 2015; Terrestrial invertebrates account for a large pro- Greenwood et al. 2018). As an annual plant, I. portion of the diversity found within riparian ecosys- glandulifera can affect riparian vegetation composi- tems. They serve as indicators of environmental tion by displacing native ruderal species (Tanner et al. conditions (Gerlach et al. 2013), perform various key 2013), which combined with fluvial disturbance functions, including pollination of invasive and native makes I. glandulifera a common and successful plant species (Bartomeus et al. 2010), and mediate the invader of riparian systems (Cˇ uda et al. 2017). Native transfer of energy between aquatic and terrestrial food plant species are displaced via direct competition for webs (Gustafsson et al. 2014; Ramey and Richardson resources, such as water and light, though displace- 2017). Riparian vegetation may significantly alter the ment may also extend to competition for pollinators allochthonous subsidy provided by terrestrial inverte- (Thijs et al. 2011). The invasive success of I. brates (Allan et al. 2003), affecting the energy glandulifera is due to a combination of tolerance for resources available to fish (Bridcut 2000; Baxter a wide range of climates and soils (Chittka and et al. 2005). However, terrestrial invertebrate com- Schurkens 2001), and an explosive seed dispersal munities are also influenced by other anthropogenic system, which facilitates its spread throughout river and environmental pressures, including land-use corridors. Fallopia japonica is an herbaceous, peren- (Newbold et al. 2015), river discharge (Sinnadurai nial plant native to China, Japan, Korea and Taiwan, et al. 2016) and shading (Feld et al. 2018). These but which is now widely established in Europe pressures may be further exacerbated by INNP, which following its introduction in the early nineteenth thereby alter the structure and functioning of the century (Beerling et al. 1994). It can recruit via several 123 All change at the water’s edge: invasion by non-native riparian plants negatively… modes, including clonal, rhizomatous growth (Aguil- by the size of INNP stands present, and as such were era et al. 2009), and quickly forms monocultures, standardised to a 20 m length of bank. Invaded sites particularly in disturbed habitats. However, F. japon- were identified provisionally on the criteria that INNP ica is also able to spread via a seed bank, and can over- coverage exceeded 50% of the vegetation cover on at winter without any negative impact on germination least one bank, whilst other characteristics should as success the following spring (Gowton et al. 2016). far as possible match those of upstream uninvaded Similarly to I. glandulifera, F. japonica displaces sites (Sax et al. 2005). However in practice, INNP native vegetation, thereby altering the composition of coverage fell below this threshold at some study sites. riparian plant communities, with consequences for aquatic and terrestrial invertebrates. Alongside normal Terrestrial invertebrate sampling and processing modes of competition (e.g. shading, monopolisation of nutrients), F. japonica also excludes native plants via Terrestrial invertebrates were collected using pitfall allelopathy (Siemens and Blossey 2007; Murrell et al. traps, each comprising a 500
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