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Durham Research Online Durham Research Online Deposited in DRO: 05 May 2021 Version of attached le: Published Version Peer-review status of attached le: Peer-reviewed Citation for published item: Sun, Jingrui and Galib, Shams M. and Lucas, Martyn C. (2021) 'Rapid response of sh and aquatic habitat to removal of a tidal barrier.', Aquatic conservation : marine and freshwater ecosystems., 31 (7). pp. 1802-1816. Further information on publisher's website: https://doi.org/10.1002/aqc.3576 Publisher's copyright statement: c 2021 The Authors. Aquatic Conservation: Marine and Freshwater Ecosystems published by John Wiley Sons Ltd. This is an open access article under the terms of the Creative Commons Attribution License, which permits use, distribution and reproduction in any medium, provided the original work is properly cited. Additional information: Use policy The full-text may be used and/or reproduced, and given to third parties in any format or medium, without prior permission or charge, for personal research or study, educational, or not-for-prot purposes provided that: • a full bibliographic reference is made to the original source • a link is made to the metadata record in DRO • the full-text is not changed in any way The full-text must not be sold in any format or medium without the formal permission of the copyright holders. Please consult the full DRO policy for further details. Durham University Library, Stockton Road, Durham DH1 3LY, United Kingdom Tel : +44 (0)191 334 3042 | Fax : +44 (0)191 334 2971 https://dro.dur.ac.uk Received: 9 June 2020 Revised: 29 October 2020 Accepted: 7 January 2021 DOI: 10.1002/aqc.3576 RESEARCH ARTICLE Rapid response of fish and aquatic habitat to removal of a tidal barrier Jingrui Sun1 | Shams M. Galib1,2 | Martyn C. Lucas1 1Department of Biosciences, University of Durham, Durham, UK Abstract 2Department of Fisheries, University of 1. River barrier removal is used increasingly as a conservation tool to restore lotic Rajshahi, Rajshahi, Bangladesh habitat and river connectivity, but evidence of its efficacy is incomplete. This Correspondence study used a before–after methodology to determine the effects of removing a Jingrui Sun, Department of Biosciences, tidal-limit barrier on the fishes, macroinvertebrates, and habitats of an English University of Durham, South Road, Durham DH1 3LE, UK. coastal stream. Email: [email protected] 2. Following barrier removal, habitat diversity increased immediately upstream and Funding information remained similar downstream. Mobilized silt altered the substrate composition European Commission, Grant/Award Number: immediately downstream, but this was temporary as silt was flushed out the fol- 689682 lowing winter. Changes to macroinvertebrate communities occurred upstream and downstream of the former barrier but these were transient. 3. A dramatic and sustained increase in fish density occurred immediately upstream of the barrier after its removal, but effects downstream were minor. The fish community upstream changed, largely due to rapid recruitment and dispersal of endangered European eel (Anguilla anguilla). Eel density in the formerly impounded zone increased from 0.5 per 100 m2 before barrier removal to 32.5 per 100 m2 5 months after removal. By 17 months after barrier removal there was no difference in eel density across the six sections sampled. 4. Although resident stream fishes such as bullhead (Cottus gobio species complex, protected under the European Habitats Directive) were abundant in middle and upper-stream sections, brown trout (Salmo trutta, a listed species for biodiversity conservation in England and Wales) density remained low during the study and recruitment was poor. This suggests that although colonization access for anadro- mous trout was available, habitat upstream may have been unsuitable for repro- duction, indicating that wider catchment management is required to complement the restoration of connectivity. 5. These findings suggest that tidal barrier removal is an effective method of restor- ing lotic habitats and connectivity, and can be beneficial for resident and migra- tory fishes including those of conservation importance (e.g. European eel) in coastal streams. This is an open access article under the terms of the Creative Commons Attribution License, which permits use, distribution and reproduction in any medium, provided the original work is properly cited. © 2021 The Authors. Aquatic Conservation: Marine and Freshwater Ecosystems published by John Wiley & Sons Ltd. Aquatic Conserv: Mar Freshw Ecosyst. 2021;1–15. wileyonlinelibrary.com/journal/aqc 1 2 SUN ET AL. KEYWORDS Anguilla anguilla, barrier removal, connectivity, dam, habitat restoration, recolonization 1 | INTRODUCTION Anguilla species (Jacoby et al., 2015). However, the occurrence of instream barriers restricting access to juvenile habitat is considered to Instream obstacles such as dams, weirs, and culverts fragment rivers be one of the major threats to the European eel population by interrupting longitudinal connectivity and altering habitat (Nilsson (Dekker, 2003; Piper et al., 2013; Tamario et al., 2019). It is also a et al., 2005; Sun, Galib & Lucas, 2020), having major effects on threat that can be responded to, through river restoration. the biodiversity and functioning of river ecosystems (Bunn & The upstream migration of juvenile European eels can last several Arthington, 2002; Pringle, 2003; Galib et al., 2018). These obstacles years, during which time they may migrate hundreds of kilometres frequently affect the dispersal and migration of fish species, and can and grow to 40 cm, although a proportion never enter fresh water result in population decline and biodiversity reduction (Lucas & (Lucas & Baras, 2001). Barriers such as weirs, dams, and sluices limit Baras, 2001; Gehrke, Gilligan & Barwick, 2002; Katano et al., 2006; their upstream migration, restricting access to suitable nursery habitat Mueller, Pander & Geist, 2011). The flow-impounding effects of river upstream (Mouton et al., 2011; Tamario et al., 2019). Although barriers result in alteration to slower, deeper, fine-sediment domi- juvenile eels, especially those smaller than 10 cm, can climb and crawl nated habitat immediately upstream, especially in low-gradient on wet and rough surfaces (Porcher, 2002; Watz et al., 2019), only reaches, with resultant effects on the biota (Boon, 1988; Mueller, a small proportion may manage to pass barriers (White & Pander & Geist, 2011; Birnie-Gauvin et al., 2017a). Barriers close to Knights, 1997; Tamario et al., 2019). Instream barriers and associated the sea can have disproportionate effects on the distribution of engineering infrastructure can reduce survival and delay the down- diadromous fish species in rivers by limiting access to suitable stream migration of the maturing silver eel stage (Behrmann-Godel & habitat upstream (Kemp & O'Hanley, 2010; Nunn & Cowx, 2012; Eckmann, 2003; Calles et al., 2010; Piper et al., 2013) before migra- Harris, 2016). tion to oceanic spawning grounds. For all diadromous species, One such species is the European eel (Anguilla anguilla), the abun- enabling their bidirectional migration in rivers is crucial (Calles & dance of which has decreased greatly since the early 1980s Greenberg, 2009). (Dekker, 2003; Henderson et al., 2012; Jacoby et al., 2015). Recruit- Although a variety of fishway designs exist to facilitate ment of glass eel (the transparent juvenile stage that enters fresh upstream or downstream migration (Silva et al., 2018), their efficacy water) has reduced by more than 90% and the population of silver eel for many species can be low (Bunt, Castro-Santos & Haro, 2012). (migrating to sea) has reduced by more than 50% (Piper et al., 2013; Eel-specific fishways pass a proportion of juvenile eel (Environment Jacoby & Gollock, 2014). Owing to its rate of decline, this species has Agency, 2011; Watz et al., 2019) but are unsuitable for most been classified as ‘Critically Endangered’ in the International Union other species. Tide flaps and management of sluices can also be used for Conservation of Nature (IUCN) global Red List (Jacoby & to support the passage of eels in tidal reaches (Environment Gollock, 2014; Pike, Crook & Gollock, 2020). Under the Water Agency, 2011; Wright, Wright & Kemp, 2015; Guiot et al., 2020). Framework Directive (WFD), European Union (EU) countries are Unlike these mitigation measures, barrier removal reinstates hydro- required to provide free migration of fishes (Council of the European logical connectivity, more natural habitat, sediment transport, and Communities, 2000), which is a particularly relevant policy tool for free movement of aquatic biota (Roni, Hanson & Beechie, 2008; supporting the recovery of European eel, as well as for other migra- Kemp & O'Hanley, 2010; O'Hanley, 2011). Removal of redundant tory fish species such as brown trout (Salmo trutta). The European barriers is increasingly used as a river management and conservation Commission also initiated an Eel Recovery Plan (Council Regulation tool in many countries (Birnie-Gauvin et al., 2017b; Silva et al., 2018). No 1100/2007) to ensure sustainable levels of adult eel abundance Several studies have measured the effects of barrier removal on geo- and glass eel recruitment across the European Union (Council of the morphological and ecological responses in rivers (Pizzuto, 2002; European Communities, 2007). Through this, EU states are required Doyle et al., 2005; Chang et al., 2017; Clark et al., 2020). For barriers to develop Eel
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