However, indirect effects of nutrient pollution are profound. For example, phototrophic hard corals can be out-competed by other benthic primary producers in high nutrient environments, leading to the establishment of macro-algae. High nutrient availability generally leads to increases in phytoplankton populations which in extreme cases reduce benthic light availability and cause seasonal hypoxia (Diaz and Rosenberg, 2008). Resultant organic enrichment can

cause a shift to heterotrophic and/or filter Fulvestrant feeding communities, and plays a role in driving population outbreaks of the coral-eating crown-of-thorns starfish (Fabricius, 2011), one of the main causes of coral cover declines on the Great Barrier Reef (De’ath et al., 2012). Overall, eutrophication can result in increased coral disease (Sutherland et al., 2004 and Vega Thurber et al., 2013) and mortality, ABT-737 nmr and contribute to loss of coral diversity, structure and function, including phase shifts to macroalgae (Fabricius, 2011). The reduction of siltation and eutrophication of coastal marine ecosystems by better managing agricultural sources at local and regional scales is a challenge for coastal communities around the world (Boesch, 2002 and Cloern, 2001), including those bordering coral reefs (Brodie et al., 2012). Globally, substantial effort is going into re-establishing environmental flows (Postel and Richter,

2003). In headwater catchments, more natural flow regimes are being reinstated through, for example, including high flows in dam releases (Rood et al.,

2005) and removing small dams and weirs (Stanley and Doyle, 2003). Ecological outcomes in downstream reaches have been documented within a year, and include formation of new river channels, restored riparian vegetation, and improved fish passage and spawning habitat (Rood et al., 2005 and Stanley and Doyle, 2003). Restoration of more natural flow regimes to coastal marine waters is being attempted through, for example, removal of large dams (Service, 2011), buying back irrigation water (Pincock, 2010) or agricultural land (Stokstad, 2008), and restoration Mannose-binding protein-associated serine protease of coastal floodplains (Buijse et al., 2002). Such larger-scale interventions have only commenced in recent years, and consequently, we were unable to find any documented examples of restored freshwater flow regimes into coastal waters (Table 1a). Nevertheless, while it is expected that freshwater flows should return to more natural regimes almost immediately, recovery of associated physical and biological processes may take years to decades (Hart et al., 2002). Despite significant investment in sediment erosion and transport control measures (Bernhardt et al., 2005), we found only one documented example of reductions in net fluxes of sediment reaching coastal marine waters following land-based restoration efforts (Tables 1b and 2).