Global challenges for seagrass conservation

Seagrass ecosystems are of global significance to our climate and food security but remain rather unknown and on the periphery of marine conservation (Duarte et al. 2008). Ensuring healthy seagrass ecosystems around the globe will be a significant action to mitigate two of humankind’s greatest challenges: feeding and supporting the needs of more than 7 billion people and achieving some level of climate stability. Seagrasses are common and form meadows in coastal environments, typically in very shallow waters down to 60 m depth. These meadows of seagrass, monocotyledonous marine angiosperms, are globally extensive and highly productive with their distribution extending to all continents except the Antarctic. Due to their capacity to bioengineer their environment, they create a complex three-dimensional habitat in otherwise structurally limited systems which support an extensive array of biodiverse fauna. Recent estimates suggest seagrass meadows support the productivity of 20% of the world’s biggest fisheries through nursery habitat provision (Unsworth et al. 2018b). Their location in sheltered shallow waters, the rich diversity of fish and invertebrate life and the shelter they provide from predation results in an abundance of animal life. This animal life is so rich and productive that wherever they are present in proximity to human populations they form a targeted fishing ground of enormous importance to human livelihoods and well-being (Nordlund et al. 2018a; Unsworth et al. 2018b). There is also growing evidence that seagrass meadows contribute to stabilising our climate through the vast storage and sequestration of carbon within their sediments (Crooks et al. 2011; Duarte et al. 2013). Overall seagrasses play a significant role in supporting a whole range of highly valuable ecosystem services that rival those of many more illustrious and well-known ecosystems such as mangrove forests and coral reefs (Nordlund et al. 2016). For example, they form vast filters of the coastal environment (both landward and seaward), cycling nutrients and reducing bacterial pathogens capable of causing disease in humans and marine organisms (Flindt et al. 1999; Lamb et al. 2017).

Our oceans and their habitats, along with the resources and services they supply, are increasingly being subjected to anthropogenic impacts and their biodiversity and productivity are rapidly being compromised (Halpern et al. 2008; Nash et al. 2017). Ocean conservation typically focusses on the charismatic habitats and species, while ignoring many of our poorly known habitats, such as seagrass, and species that are of major significance to responding to the challenges of climate and food security. The conservation of lesser known habitats remains problematic in light of limited and finite conservation resources.

The great challenge for seagrass ecosystems is that they’re threatened globally, with evidence indicating accelerating rates of loss and degradation (Waycott et al. 2009; Unsworth et al. 2018a). Their common shallow water presence at the coastal-land interface makes them highly vulnerable to disturbance and anthropogenic impact. Given the marginalisation of these ecosystems on the world conservation agenda, understanding how we can reverse this trajectory of loss is vital. Declining coastal water quality from catchment degradation, pollutants and poor coastal zone management is placing untold pressures on seagrass ecosystems. In addition, overfishing, land reclamation, boating and aquaculture are also significant threats to seagrasses around the world (Grech et al. 2012). We need to implement effective management strategies to reverse seagrass loss and enhance their fundamental role in food provision and climate stability. In order to do this we need to understand the challenges these systems face from a multifaceted and interdisciplinary perspective, as well as identifying actions to mitigate these challenges.

Here we propose that seagrass meadows globally face a series of significant common challenges that must be addressed in order to achieve global conservation goals. We also explicitly outline a series of proposed actions that will enable the scientific and conservation community to rise to these challenges. While some of the problems outlined in our challenges are generic to many marginalised ecosystems, we believe the global nature of seagrasses, their low species diversity but high ecosystem service value, and their unique role in supporting human livelihoods mean the nature of many of these challenges are also unique to seagrass. We believe that the most significant of these challenges is a lack of societal recognition for their importance, the consequences of which are linked in at least some way to all the other challenges.

The greatest challenge for global seagrass conservation is to enhance societal awareness of the importance of seagrass ecosystems so that bold management and restoration decisions can be met with public support (Duarte et al. 2008). Recognition of what seagrasses are and their functional contribution to human well-being remains limited in many parts of the world (Cullen-Unsworth et al. 2014). Given that seagrass is a global resource, many people have never heard of it, or they confuse it with seaweed (algae) (Jefferson et al. 2014). Where fishers depend on seagrass for livelihoods, recognition of their importance is high (Newmaster et al. 2011). But where people are removed from direct experience, or when the ecosystem service provided is indirect (e.g. the value of seagrass as a nursery ground for supporting major fisheries), recognition of what seagrass is and its importance is poor. Raising awareness is a critical challenge that addresses the widespread extent of ill-informed decisions made (from individual to government action) that contribute to continued seagrass loss and degradation.

Limited societal recognition of seagrass is exacerbated due to its apparent charisma problem in comparison with other highly charismatic habitats such as coral reefs (Duarte et al. 2008). The general public, politicians, decision makers, business leaders and all other stakeholders need to be better informed about how seagrass meadows contribute to our economies and our planetary well-being (Cullen-Unsworth et al. 2014). As the human population becomes more urban, biodiversity conservation becomes harder to achieve as a result of what has been termed the ‘extinction of experience’ (Miller 2005). People are becoming increasingly disconnected from the natural environment and direct experience with nature appears to be a prerequisite for environmental action (Dunn et al. 2006).

Wider understanding of the natural environment and its importance to people helps build social capital, increasing the tendency to change behaviour in response to environmental concerns (Pretty and Smith 2004) such as seagrass loss. Recognition by the general public does not just lead to altered personal action but can lead to pressure on policy-makers to act and empowerment of regulators to find solutions. Minimal public awareness denotes limited pressure from the public on management authorities and regulators who, as a result, are not sufficiently empowered to take action against individuals and companies responsible for seagrass damage (e.g. widespread boating damage).

To increase awareness of seagrass, we firstly propose to enhance education and experience opportunities for people of all ages. People need to experience seagrass for themselves as experiencing nature empowers people to act (Campbell et al. 1999). If we are to nurture future environmental leaders and encourage more seagrass conservation action, we need to ensure that more people have access to nature (Dunn et al. 2006). Awareness of seagrass may change with respect to locality, as research in different localities (e.g. UK vs. Tamil Nadu in India) indicates very different levels of seagrass awareness (Newmaster et al. 2011; Jefferson et al. 2014). Whether such differences exist over different levels of economic development remain unclear but studies on local ecological knowledge indicate decreasing knowledge with economic development (Pilgrim et al. 2008). As shallow intertidal to subtidal environments, seagrass habitats are highly accessible either on foot or with simple snorkelling equipment. As such they make great places to experience nature. Programmes that encourage human–nature interactions (e.g. seagrass citizen science) (Jones et al. 2018) need to be expanded to increase the opportunities for stakeholders to learn about and engage with seagrass and participate in their conservation.

Secondly, seagrass conservation needs to encompass research and experience from other fields of science communication and environmental management. For example, communicating climate science has been enhanced by adopting interdisciplinary approaches, such as inclusion of psychology and sociology to understand human reactions (Stern 2011). For example, the use of psychology could be a way of helping find a way to overcome ‘image problem’ of seagrass through the development of improved marketing and education materials. Finally, those involved with the conservation of seagrass ecosystems also need to work more closely with the global media to better highlight and communicate the value, necessity and beauty of seagrass (see Fig. 1 and Supplementary Video). Great strides have recently been made in this field through the development of the major BBC series ‘Blue Planet II’ that included extensive seagrass coverage. This progress needs to be built upon using the expanding technologies of virtual reality and 3D filming. Only through increased experiential learning opportunities, broadening conservation efforts across disciplines, and developing collaborations with global media will we be able to increase societal recognition of seagrass importance and positively impact conservation efforts.

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Improved spatial assessments need to be accompanied by more widespread seagrass health and risk assessments so that early warnings of seagrass decline are available and that subsequent management measures can be taken to reverse degradation. Currently, indicators used to measure seagrass condition (e.g. biodiversity, distribution and abundance) are spatially or temporally limited. As a consequence, no globally complete database of seagrass extent or condition exists from which reference baselines can be established. Temporal data on seagrass extent are limited to sub-regional scales, for example in Denmark where nation-wide records extend for over a century (Riemann et al. 2016) and NE Australia and the western Mediterranean where only scattered decadal-scale observations are available (Rasheed and Unsworth 2011). The adoption of seagrass as a robust indicator of the health of coastal ecosystems in programmes such as the EU Water Framework Directive (Roca et al. 2016), the Chesapeake Bay (US) Program (IAN 2017) or Australia’s Great Barrier Reef Water Quality Protection Plan (McKenzie et al. 2012) have created platforms for sustained monitoring across sub-regions, but such programmes are scarce and in some cases require improvement. A significant gap in such monitoring is within developing countries that often do not have the financial resources necessary for such monitoring programmes. Such monitoring approaches need to be expanded to include all regions of the world. To rise to the challenge of mapping the world’s seagrass, first we need to rationalise disparate available data into a single resource, essentially updating the UNEP-WCMC Global Distribution of Seagrasses database (UNEP-WCMC and Short 2016), identify present data gaps and develop and standardise efficient mapping tools.

Secondly, given the extensive gaps in our global seagrass distribution database there is not a one-size-fits-all solution to this challenge. To fill these data gaps approaches need to be both top down (habitat suitability modelling and remote sensing) and bottom up (infield targeted assessments). A concerted effort, using shared reporting platforms yet to be developed, is needed from the highest levels of conservation (e.g. large international NGOs, IUCN/UNEP and governments) to the smallest of community groups. Mapping needs to harness the best features of new technology (e.g. phone apps, drones, remote sensing) as well as traditional and novel approaches (e.g. tagging of migratory seagrass-associated fauna). Furthermore, in the endeavour to map the world’s seagrasses connecting with new groups of people potentially increases the scale of available observation resources (e.g. citizen scientists) (Jones et al. 2018) and stakeholders previously not engaged in research activity (e.g. financiers involved with Blue Carbon).

Third, seagrass habitat suitability (Gattuso et al. 2006) and niche-based (Chefaoui et al. 2016) models offer major opportunities, as future mapping activity can target areas identified as potential seagrass habitats. For these models to be more effective, they require improved biophysical datasets (e.g. bathymetry and bottom substrate, seawater temperature at locations where seagrass and present and absent) that adequately represent the environmental requirements of seagrass. This requires close working of seagrass scientists with other disciplines such as oceanography to improve acquisition and availability of relevant data.

In order to rise to the challenge of understanding local-level threats to seagrass, we believe that incorporating local ecological knowledge (LEK), including indigenous knowledge and other expert witness knowledge as alternative data sources, is key (Grech et al. 2012). Recognising the value of LEK increases stakeholder participation and commitment with management and conservation schemes (Nordlund et al. 2018b). The use of LEK can help lead to the development of spatially explicit marine conservation decision making (Grech et al. 2011) and to the creation of effective conservation management actions that form the basis of behavioural change that targets previously overlooked threats (see Box 2).

Yet, while recognising the key value of addressing local factors, evidence that seagrass ecosystems are vulnerable to ocean warming is mounting (Marba and Duarte 2010), requiring seagrass conservation efforts to extend to support efforts to mitigate climate change under the goals of the Paris Agreement, where seagrass conservation as part of blue carbon strategies is included within multiple National Declared Objectives (see Challenge 6).

A major challenge in securing a future for seagrass meadows lies in achieving a balance between the objectives of environmental, ecological and socio-economic sustainability associated with this habitat. Seagrass meadows are recognised social-ecological systems that contribute significantly to the well-being of people and planet (Cullen-Unsworth et al. 2014). The location of seagrass meadows largely at the land to sea interface makes them extremely valuable to coastal peoples, particularly in developing regions where intertidal gleaning fisheries in seagrass can be critical for the subsistence of many people. But this positioning adds to their vulnerability where they are subject to multiple uses and multiple stressors from both land- and sea-based sources (Nordlund et al. 2014). Conflicts appear to exist between the needs of biodiversity conservation and the continued supply of seafood (Salomon et al. 2011).

We need to move away from notions considering humans as external agents of disturbance to a previously well-functioning ecosystem. We need to instead build an inclusive framework including humans as part of the ecosystem conducive to a sustainable and resilient future for people and planet together. The 17 Sustainable Development Goals (SDGs) of the 2030 Agenda for Sustainable Development (that superseded the Millennium Development Goals) reflect this notion and officially came into force in January 2016 (UN 2017). The SDGs apply to all countries who are expected to mobilise efforts to end poverty, fight inequality and tackle climate change. To have any chance of success, recognition in planning, monitoring and management, that ecosystems are inherently coupled social-ecological systems (SES), is the only reasonable way forward. Considering seagrass habitats within an SES framework is the most promising path to actualise successful seagrass monitoring, management and inclusion in planning processes. To do so, an integrated SES approach is needed at a variety of social and ecological scales (Hessing-Lewis et al. 2017). Sustainability is not a pseudonym for environmental conservation, as creating sustainable places requires biophysical, economic and socio-cultural sustainability at the ecosystem and increasingly at the global scale.

We need to embed conservation in a broader, multidimensional effort towards sustainable ecosystems, rather than have conservation as a stand-alone goal excluding the communities that use the ecosystems. First, we propose that to rise to the challenge of creating sustainable places we need research to expand our understanding of the interactions between the socio-economic and ecological elements of seagrass systems. This requires transdisciplinary approaches, bridging the divide between scientific disciplines (Salomon et al. 2011) and establishing encompassing partnerships with practitioners and other stakeholders (Lang et al. 2012).

Second we need data on the fishery activity in seagrass, as this is a significant component of the role of seagrass meadows as social-ecological systems (Nordlund et al. 2018a). Data are available on some commercial seagrass fisheries, but data from the collectively significant small-scale fisheries that seagrass meadows support are highly limited (Nordlund et al. 2018a). Making effective management decisions for seagrass meadows requires understanding the diversity of seagrass fisheries in terms of their economic, cultural, institutional and social values, as well as characterisation of the ecological and environmental variables. We need to rectify this in order to better target management action. We also need to improve catch monitoring of seagrass fishery activities and collect data on other fishery characteristics, in particular, fisher demographics, because too broad assumptions can lead to misguided management decisions.

Finally, we highlight that to respond to the challenge of balancing the needs of people and planet we need to recognise that seagrasses are part of a connected social-ecological system at catchment and seascape scales (de la Torre-Castro et al. 2014). Ecosystem-based management that goes beyond current geographical or habitat boundaries to encompass whole catchments needs to be more widely developed. In support of these approaches, we further need to campaign for integrated policies that seek win–win opportunities in reconciling the protection of habitats and species with the maintenance of other ecosystem services such a food security simultaneously.

A major hurdle to overcome the four challenges described above is the limited effort allocated to seagrass research and conservation, particularly when compared to other coastal and nearshore habitats. Not only is this a current problem, but we present evidence that the problem is rapidly getting worse (Box 3; Fig. 2). We suggest a major proximate cause is the fact that there are relatively few researchers studying seagrasses, particularly in relation to their widespread, near-global distribution (Hind-Ozan and Jones 2017) (see Box 3). This minimal and geographically concentrated seagrass research effort creates obvious challenges in generating and generalising research outcomes, particularly for conservation. For example, seagrass research is heavily skewed towards a few genera like Zostera, Thalassia and Posidonia (Nordlund et al. 2016) and for many other species we lack fundamental understanding about their distribution as well as their biology. Undoubtedly, this lack of understanding makes it difficult to manage seagrasses effectively and is exacerbated in many developing countries by funding difficulties and in some instances limited scientific capacity. Second, in many cases we do not yet understand the physical, chemical and biological attributes that combine to support the provision of different seagrass ecosystem services (Nordlund et al. 2016). Third, climate change research is perhaps one of the fastest growing sub-fields in seagrass ecology, but we still lack a predictive understanding of how global environmental change will influence seagrasses, the ecosystems they create and the services they support (see Challenge 6).

Box 3 Increasing imbalance in seagrass research funding and effort

A decade ago, Duarte et al. (2008) (Duarte et al. 2008) demonstrated that coral reefs received far more research effort and media attention than seagrasses, mangroves and salt marshes. This is despite the wide occurrence and societal importance of all four ecosystems. Here, we show that although there has been a considerable increase in seagrass research and conservation effort, the imbalance has in fact increased over time. This involves both research funding, effort, and the proportion of general ecology and ecosystem research that this effort constitutes. First, data on private research and conservation funding 2006–2016 (retrieved from the Foundation Center database: foundationcenter.org) show that the number of grants and the total funding to grants including the word ‘coral’ exceeded those to ‘seagrass’, ‘mangrove’ and ‘marsh’ grants by 1–2 orders of magnitude (Fig. 2a). Moreover, the ‘coral’ grants were allocated to > 1 order of magnitude more recipients (researchers, practitioners, etc.). Second, data on research effort over the past 25 years (estimated as yearly number of publications in ISI Web of Science during 1992–2016) show that publications including the word ‘coral*’ in title, abstract or keywords not only dominate (Fig. 2b), but that ‘coral’ and ‘mangrove’ research effort has grown exponentially. At the same time, ‘seagrass’ and ‘salt marsh’ effort has only grown linearly and considerably slower. Finally controlling for the fact that ecology and ecosystem science in general has grown considerably (by calculating what proportion of yearly publications retrieved using the search string ‘ecosystem* OR ecolog* OR species*’ that also included the words ‘coral*’, ‘mangrove*’, ‘seagrass*’ or ‘salt marsh*’), a striking pattern emerges. The proportion of publications increased more or less linearly for all four ecosystems until the mid 2000s (indicating an increasing interest for and/or effort in coastal ecosystem research), after which the proportion of ‘coral’ and ‘mangrove’ research effort kept rising, but the proportion of ‘seagrass’ and ‘salt marsh’ publications instead levelled off and decreased. Together, these results suggest that seagrass (as well as salt marsh) research and conservation is underfunded, conducted by fewer people, and grows at an increasingly slower rate, than that on coral reefs (and to a lesser extent mangrove) (Fig. 2).

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Seagrass conservation is also made difficult by the fact that there is often a mismatch between research funding and conservation needs. The need for additional research in support of more effective conservation might not always be obvious to decision makers or even researchers themselves. Additionally, we present data that indicate the charisma gap of seagrass ecosystems makes it difficult to find funding for seagrass research (Box 3). This is especially so for seagrass conservation-related research, particularly when competing to other, more charismatic coastal habitats. The need for novel science and the drive for researchers to publish unique findings can skew our understanding of seagrass ecosystems, e.g. by limiting local or regional study replication. Reports on simple observations of seagrass distribution, abundance and functional traits are required that are vital for making key management decisions. These data are particularly required from underrepresented areas, to avoid such biases in our knowledge. Descriptive, long-term time series of seagrasses and associated organisms, and spatially extensive surveys along natural and human-induced environmental gradients, are expensive and difficult to sustain in a research funding climate rewarding quick research output through short-term projects, but critically needed to understand seagrass ecosystem dynamics and response to local and global changes.

Wider interest in seagrass research across disciplines is growing and this needs to be built upon (Hind-Ozan and Jones 2017). First, research areas where seagrasses are already receiving considerable attention—e.g. seagrass meadows as blue carbon sinks (Fourqurean et al. 2012), the role of seagrasses for food security (Nordlund et al. 2018a; Unsworth et al. 2018b)—could be used to gain a broader interest in seagrasses from other researchers and students currently working on other systems, and motivate research about other aspects of seagrass biology. This also creates opportunities for seagrass research to integrate into wider studies about the connected coastal seascape. Second, while much seagrass research is specialised and aimed towards other specialists, there is a rapidly increasing body of high-profile studies demonstrating that the use of seagrasses as a model system to test broader questions—both fundamental and applied—can greatly increase interest in seagrasses. A few noteworthy examples include the use of seagrass to understand genome changes for angiosperms to colonise the sea (Olsen et al. 2016), the role of seagrass in removing pathogens from the water column (Lamb et al. 2017), the importance of symbiotic associations in seagrass ecosystems (van der Heide et al. 2012), the role of seagrass genetic diversity to buffer effects of disturbance (Reusch et al. 2005), and the relationship between biodiversity and ecosystem functioning (Duffy et al. 2015). While some of these studies are seagrass-specific, most target seagrasses because they constitute an ideal model system, have a relatively low (and therefore manageable) species diversity, occur along most sheltered coastlines, are relatively easy to access, and are easy to manipulate in situ, collect and grow.

Third and finally, seagrass researchers need to better communicate their research findings to a broad audience interested in marine life and the ocean, but must do so by placing seagrass as part of a wider connected seascape. Social media and online networks (e.g. Twitter, Instagram, Facebook, etc.) are simple yet powerful tools that can be used by individual researchers to spread interest in seagrasses, their ecology and their conservation to other researchers and the general public with limited effort (Hind-Ozan and Jones 2017). Although online communication tools are the necessity for science outreach in much of the globe, the internet remains a privilege of only half the worlds’ population (Sample 2018). In some nations, the use of traditional tools such as newspapers and radio may be more appropriate means of sharing scientific information than through social media.

Climate change is the most widespread anthropogenic threat to marine ecosystems. Direct impact to seagrass meadows include greater physical disturbance due to increasing storm frequency (Brierley and Kingsford 2009), rising water temperatures (Hyndes et al. 2016), reduced light due to sea-level rise (Grantham et al. 2011), and rising CO₂ levels in coastal waters (Brierley and Kingsford 2009). Physiological responses to shifting environmental conditions result in species range-changes (Hyndes et al. 2016), localised invasions and extinctions (Mellin et al. 2016), and shifts in the structure and function of seagrass meadows (Björk et al. 2008). As a result, not only is the physiology of seagrass species affected by climate change but also their interactions with each other and their environment (Hyndes et al. 2016). In many regions, current legislation protecting marine resources do not expressly consider natural climate variability or anthropogenic climate change. As legislation comes up for cyclical reviews, it is important for legislative directives to move beyond focusing on mitigation (Nachmany et al. 2014) to also include adaptive and responsive mechanisms that deal directly with current and projected impacts of climate change on coastal habitats including seagrass meadows (Frost et al. 2016).

First, habitat protection policies need to incorporate projected future distributions of seagrass meadows rather than focusing on past conditions. Many species are unable to acclimate to new climate conditions, or adapt to the unprecedented pace of contemporary climate change (Collier et al. 2017). Some seagrass species, such as the Mediterranean endemic Posidonia oceanica, are already experiencing significant mortality with ocean warming (Marba and Duarte 2010) and are forecasted to experience dramatic losses with further warming (Jordà et al. 2012). Alternatively some seagrass species are predicted to move to track the poleward shift of isotherms (Poloczanska et al. 2013) and eventually expand into the Arctic (Krause-Jensen and Duarte 2014). In western Australia, temperate seagrasses have already contracted their ranges in response to warming ocean temperatures (Hyndes et al. 2016) and tropical ecosystems are expected to further shift their ranges as temperatures continue to warm (Vergés et al. 2014). These shifts may have significant impacts on biodiversity within seagrass meadows, especially in species rich equatorial and coastal regions (Collier et al. 2011). Researchers need to provide robust predictive models of future habitat distributions to environmental managers to enable the flexibility within policy for future changes in habitat distributions.

Secondly, seagrass monitoring should report on indicators that provide an early warning of reduced resilience, breaks in connectivity and imminent range shifts. Loss of genetic diversity affects resilience through recovery and adaptive capacity, with populations near the edge of distributional ranges being most affected (Reynolds et al. 2016). Therefore, a loss of genetic diversity could be an early-warning indicator of loss of resilience and the potential for range contraction, particularly when it is impractical to monitor distributional ranges. Quantifying the density and viability of seagrass seed banks can also provide a measure of seagrass resilience as germination of seeds and the development of seedlings provides a recovery mechanism following large-scale declines (Jarvis and Moore 2010). Finally, efforts must be made to conserve connectivity between populations and to conserve links between source and sink populations for seagrass propagules (McMahon et al. 2014) including the protection of biological dispersal agents (e.g. megaherbivores Tol et al. 2017). One possibility would be to move away from static MPAs to connectivity-informed MPAs that are spatially designed to maximise connectivity between source and sink populations or dynamic MPAs that adjust for changing species distributions.

Thirdly, environmental targets that are set for seagrass conservation (e.g. water quality guidelines) should move towards future climate adjusted targets and allow for cumulative impacts and ecological feedbacks (Maxwell et al. 2017). For example, elevated water temperature increases seagrass light requirements (Collier et al. 2012) and both elevated temperature and low light create a negative feedback at the sediment-plant scale (Koch et al. 2007). If these interactions and feedbacks are quantified, they can be accommodated in water quality guidelines. Similarly, the timing of other anthropogenic disturbances can be managed to avoid unnecessary cumulative impacts, e.g. dredging at a time of greatest risk from extreme temperature (Wu et al. 2017). Sub-lethal indicators with a distinct cause–effect pathway can also provide ‘real-time’ feedback when environmental targets are breached (McMahon et al. 2013). These early-warning signs can enable management prioritisation and set associated achievable management goals to minimise the risk of cumulative impacts including climate change.

Finally, active intervention strategies such as innovative restoration techniques will be increasingly required to repair ecological function following disturbances, and need to be adaptable to changing climatic conditions (Timpane-Padgham et al. 2017). Changes in flowering effort, frequency and timing within species lifecycles in response to warming temperatures have also already been observed for seagrasses around the world (Jarvis et al. 2011; Suonan et al. 2017). These heat-adapted populations may provide suitable restoration propagules for those that do not have heat resistance, but face increasing temperatures. However, not all species have shown potential for natural acclimation (Collier et al. 2017), in which case additional strategies may be required to maintain ecological function.