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    Managing the public health paradox: Benefits and risks associated with waterway use
    Anne Roiko1,2, Sonya Kozak1, Anne Cleary1 and Zoe Murray1
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Managing the public health paradox: Benefits and risks associated with waterway use

Authors
Anne Roiko1,2, Sonya Kozak1, Anne Cleary1 and Zoe Murray1
Author affiliations
  1. School of Medicine, Griffith University,
  2. The Hopkins Centre, Griffith University
Corresponding author
a.roiko@griffith.edu.au
Book

Moreton Bay Quandamooka & Catchment: Past, present, and future

Chapter

Chapter 2 Communities and Values

Research Paper Title

Managing the public health paradox: Benefits and risks associated with waterway use

Cite this paper as:

Roiko A, Kozak S, Cleary A, Murray Z. 2019. Managing the public health paradox: Benefits and risks associated with waterway use. In Tibbetts, I.R., Rothlisberg, P.C., Neil, D.T., Homburg, T.A., Brewer, D.T., & Arthington, A.H. (Editors). Moreton Bay Quandamooka & Catchment: Past, present, and future. The Moreton Bay Foundation. Brisbane, Australia. Available from: https://moretonbayfoundation.org/

DOI

10.6084/m9.figshare.8072546

ISBN

978-0-6486690-0-5

Abstract

Engaging with waterways affects our health and wellbeing. This engagement can be direct and intentional, such as when swimming, kayaking or engaging in conservation practices; indirect and intentional, such as when picnicking with water views; or incidental, such as when cycling on riverside bike paths. In the subtropical climate of the Moreton Bay catchment these activities are popular year-round. These forms of engagement can benefit our physical, mental and social wellbeing, and contribute to our cultural identity and sense of place. Conversely, there are health risks associated with waterway use, including exposure to waterborne pathogens, cyanobacterial toxins, dangerous aquatic animals and submerged objects. Whether our interactions with waterways enhance our health and wellbeing or constitute a health risk depends on a wide range of factors and management decisions. In the context of the waterways within Moreton Bay, this paper discusses ways of optimising opportunities for water users while managing public health risks, and how to evaluate the effectiveness of interventions through the use of environmental health indicators.

Keywords: recreational water, ecosystem health, wellbeing, DPSEEA, indicators

Introduction

‘Healthy waterways, healthy people’— the connection is intuitive. Images of clear, blue rivers, lakes, waterfalls, beaches and oceans feature in tourism brochures as a backdrop to vibrant backpackers engaged in exciting water sports or families relaxing alongside tranquil water bodies. From the upper reaches of tributaries in sub-catchments of the Brisbane River through to Moreton Bay, this region provides a diverse range of water-based environments that impact on the health and wellbeing of individuals and communities. The state or condition of these aquatic environments and how we interact with them (directly and indirectly) are critical factors that determine whether health outcomes are positive or negative (1). Degraded, polluted waterways can result in adverse health due to direct exposure to pathogens or toxins or by providing habitats for disease vectors such as mosquitoes (2, 3). On the other hand, healthy waterways can be ‘health-promoting’ by providing locations suitable for swimming and other forms of physical activity, as well as spaces for stress relief, relaxation and social interaction (4). The aim of this paper is to consider the risks and health benefits associated with waterways in general, with a specific focus on the Moreton Bay region. It conceptualises the relationships between waterways and human health by drawing on trans-disciplinary constructs and international frameworks.

The complexity and richness of the relationships between waterway health and public health warrant a deeper analysis. The intrinsic and reciprocal relationships between human and ecosystem health were synthesised through the Millennium Ecosystem Assessment (MEA), framed around the construct of ecosystem services (5). The MEA describes ecosystem services as the benefits we acquire from ecosystems, which include our waterways. These services can be ‘provisional’ (e.g. providing water and food), ‘regulatory’ (e.g. regulating water supplies, climate and diseases), ‘cultural’ (e.g. being a medium for recreational, aesthetic, spiritual and educational pursuits) and ‘supportive’ (e.g. supplying nutrient recycling systems). Human wellbeing is intrinsically linked to ecosystem health through the benefits arising from meeting our basic resource needs, social relations and access to resources that will mediate the security of health and sustained quality of life, including food and water security. Thus, protecting the health of waterways has both intrinsic value to these ecosystems and reciprocal value to public health.

Utilising ecosystem services at unsustainable rates will not translate to proportionately larger public health benefits. Similarly, when an ecosystem service is scarce, any small decrease ‘can substantially reduce human wellbeing’ (5 p49). While better access to ecosystem services has provided human societies with the means to improve health and wellbeing, society may be forcing irreversible changes and damage to these ecosystems. For example, although societal factors such as changing demographics, economic policies, governance frameworks, scientific and technological developments, and cultural and religious choices can improve human health, they can also become indirect drivers of significant pressures on ecosystems. Detrimental changes to ecosystems have resulted from intensive land use, the introduction of exotic species or extinction of native species, inappropriate technologies, the excessive use of chemicals, over-harvesting and over-consumption.

Human health cannot be isolated from the health of ecosystems. Nine categories of indicators of health outcomes related to wetland[1] ecosystem services have been identified by Horwitz and Finlayson (1): (i) contributors to hydration and safe water, (ii) contributors to nutrition, (iii) sites of exposure to pollution or toxicants, (iv) sites of exposure to infectious diseases, (v) settings for mental health and psychosocial wellbeing, (vi) places from which people derive their livelihood, (vii) places that enrich people’s lives, and enable them to cope and help others, (viii) sites of physical hazards, and (ix) sites from which medicinal and other products can be derived. It is, however, restrictive to consider that ecosystems deliver only a one-way service and that only humans benefit from a healthy ecosystem—this risks ignoring the reciprocity of the human–ecosystem relationship and the human contribution (improvement, maintenance, degradation) to the health of the ecosystems described by Horwitz & Finlayson and Comberti et al. (1, 7).

The relationships between human health and the ecosystem services provided by waterways are not linear and can be paradoxical. Depending on how they are managed, wetlands can either enhance or diminish human health via effects on their ecological functioning and ability to provide the various ecosystem services from which we benefit (8). For example, trade-offs are made when engineering works carried out to regulate rivers for flood mitigation in order to protect lives and property in a way that may diminish some of their other intrinsic ecosystem services. On the other hand, river reaches could be managed in a way that enhances their aquatic ecosystem health by slowing down the water and creating habitats using large woody debris, but at the expense of safe swimming or boating. A framework for making these trade-offs and paradoxes explicit was first presented in Horwitz & Finlayson (1) and adapted slightly in Finlayson & Horwitz (6). This defined four possible relationships to consider when relating the condition of ecosystem services and human health:

  • Double dividend – improved health outcomes and enhanced or maintained ecosystem services
  • Environmentalist’s or Wetlands paradox – a degraded ecosystem which provides positive health outcomes (e.g. draining wetlands or applying pesticides to control disease vectors)
  • Paradox of the health imperative or Health paradox – a maintained or enhanced ecosystem can pose negative human health consequences (e.g. protected wetlands providing ideal mosquito breeding sites)
  • Unhealthy wetlands – a poor human health outcome associated with degraded wetlands.

These relationships are depicted in Figure 1.

Relationships between ecosystem services and human health
Figure 1. Four relationships possible when considering the condition of ecosystem services and human health (1 p. 684).

Wise stewardship of places such as Moreton Bay and its catchment should aim for the double dividend of healthy people and healthy wetlands. This requires an understanding of how these complex relationships operate and change across the catchment and sub-catchments of Moreton Bay and over time. As a starting point, this would require multiple measures of both aquatic ecosystem health and human health and wellbeing so that these trade-offs could be made explicit.

Health benefits and risks associated with the use of waterways

The  use of natural waterways provides health benefits yet presents potential health risks. The health benefits of water-based recreation are widely accepted (2, 4, 9). It is also well established that exposure to poor-quality recreational waters can result in negative outcomes for human health (10, 11). These health risks and benefits derive from exposure to environmental health determinants that are physical, microbial, chemical, psychological or social. Table 1 summarises both the health risks and benefits associated with using waterways under these five categories of health determinants. In order to maximise their public health benefits, waterways must be managed such that human exposure to hazards is minimised without placing undue restrictions on waterway use (2).

Table 1. Health risks and benefits associated with the use of waterways.

Type of health determinant Health risks associated with waterways Health benefits associated with waterways
Physical
  • Injuries sustained during recreational activities (e.g. jetski collisions, sunburn, trip hazards, drownings, and bites/stings from dangerous aquatic organisms) (12)
  • High turbidity due to high sediment loads can increase the likelihood of physical injuries due to poor visibility, while also reducing the efficacy of UV disinfection of microbial contaminants (12)
  • Personal security risks (e.g. muggings in poorly lit areas)
  • Deterioration of water quality or water sites may impede participation in physical activities (8)
  • Improved physical health (e.g. through use of walking trails and water sports such as swimming, surfing, fishing and wading) (4)
  • Buffering from extreme events (e.g. flooding) (6)
  • Climatic regulation, mitigating the heat-island effect (13)
  • Benefits of moderate sunlight exposure (e.g. vitamin D synthesis) (12)
  • Provision of food and water (5)
Microbial
  • Ingestion of waterborne pathogens (e.g. Cryptosporidium, Giardia, Campylobacter spp.)  and adenoviruses in water contaminated by sewage and/or stormwater (12, 14)
  • Infection by water-based pathogens (e.g. Leptospires and Naeglaria fowleri) (12, 14)
  • Infection by pathogens spread by insect vectors that breed or bite near water (e.g. Ross River virus infection) (12)
  • Pathogens associated with engineered water systems including water parks (e.g. Pseudomonas aeruginosa) (15)
  • Bioregulation of pathogens via predation/competition (12)
  • Sequestration of pathogens by natural vegetation (16)
  • Protection against conditions fostering pathogen growth  through intact riparian zones (e.g. increased sediment, temperature and nutrient levels) (12)
Chemical
  • Exposure to cyanobacterial toxins (e.g. Lyngbya majuscula)(17)
  • Reduced exposure due to pollutant filtration by wetlands (18)
Psychological
  • Loss of relaxing/stress-reducing aesthetics (6)
  • Solastalgia – existential distress caused by environmental deterioration or loss (19)
  • Improved psychological health (2)
  • Nature contact is associated with reduced mental ill-health (e.g. stress, anxiety and depression) and promotion of wellbeing (20).
Social
  • Loss of sense of place and/or cultural identity (2)
  • Deterioration of water quality or water sites may impede opportunities for social interaction (2)
  • Improved community cohesion (21)
  • Enhanced sense of place (21)

 

Physical hazards present the highest health risk to recreational water users (10, 12). Incidents of drowning, major impact injuries, and slip, trip and fall injuries can result in death or permanent disability. As a result, recreational water management programs should consider the physical characteristics of a beach or other water environment, including water depth and turbidity; swimming zone topography; presence of breaking waves, currents and rips; and local and foreign hazards such as coral reefs or floating debris (12). The risk of these hazards may be compounded by exposure to solar radiation, heat and cold (12). In addition to natural hazards, incidents of violence from other people may result in physical harm (e.g. muggings in remote or poorly lit areas).

The health benefits associated with physical aspects of waterways are probably the most intuitive. At the most basic ‘sustenance’ level, waterways provide food (via wild-caught and farmed seafood and crop irrigation) and sources of raw water for drinking. During extreme climatic events, such as the Brisbane flood of  2011, waterways can protect lives and property through peak discharge attenuation (22). Even small urban creeks within built environments can reduce the urban heat-island effect considerably (13, 23). The ‘everyday health dividends’, on the other hand, are the physical health gains derived through a wide range of recreational and sporting activities such as swimming, surfing, fishing, kayaking and walking along trails near waterways (4). In addition, these outdoor activities provide the co-benefit of vitamin D being synthesised in our bodies in sufficient amounts.

Microbial hazards, particularly pathogens, are of high public health concern. Pathogenic bacteria, viruses, protozoa and helminths have the potential to cause a wide range of acute, delayed, chronic and fatal health conditions (12). Major point-sources of such pathogens include faecal pollution from wastewater treatment plants, sewer overflows and industrial effluents (2). Non-point sources include water runoff from surrounding landscapes, defective sanitation systems (e.g. onsite septic systems), as well as agricultural run-off and faecal pollution from bathers, wildlife and domestic animals (14). Human faecal pollution is considered to pose substantially higher health risks than other animal wastewater (24, 25), particularly due to potential exposure to human enteric viruses (25). Globally, epidemiological evidence shows that gastroenteritis (with symptoms such as diarrhoea and vomiting) is one of the most common diseases caused by a range of human pathogens via exposure to contaminated waters (2, 14). Routine microbial water quality monitoring of recreational waters in Moreton Bay by local authorities is generally limited to faecal indicator bacteria (Enterococci). Regular exceedances of recreational water guidelines (e.g. where 200–499 Enterococci CFU/100mL triggers additional investigation and ≥500 Enterococci CFU/100mL triggers temporary site closure for recreation, CFU – colony forming units) occur particularly after heavy rainfall (26). While these data are not generally available to the public, the general advice provided on the Healthy Waterplay website is to avoid swimming during, and at least one day after, heavy rain in open waterways and beaches, and for at least three days within confined bays and estuaries (27). Brisbane City Council is one of the authorities that does publish its microbial water quality data (28). Despite these exceedances, epidemiological evidence of outbreaks of gastro-intestinal illness associated with recreational use of these sites is lacking.

Not all microbes in and around water are harmful. Recent developments in metagenomics have unveiled the importance of microbial biodiversity by allowing us to profile the bacterial communities associated with specific aquatic environments. Studies conducted by Beale et al. (29) in variably polluted reaches of the Brisbane River have used metagenomics to better characterise the responses of bacterial communities to contaminants. Research in this emerging field suggests that diverse bacterial communities play a crucial role in ecosystem health resilience and the recovery of areas following pollution events (30, 31). This resilience and recovery may play a factor in regulating which water-based recreational activities can resume and when following pollution incidents.

Chemical hazards in our waterways can present health risks under certain exposure scenarios. Actual levels of health risk are determined by the characteristics of the chemical, exposure routes and pathways, the nature and magnitude of exposures, and the characteristics of the individuals and populations exposed (32). Chemical toxicants can enter waterways rapidly via a massive influx (chemical spill) or very slowly and imperceptibly over time via complex pathways. The former often triggers a public health response that minimises exposure and therefore the health risk, whereas the latter can lead to chronic, biomagnified exposures via the food chain (18). At commonly observed concentrations, chemical hazards in recreational waters typically pose a lesser threat to public health compared with the other types of hazards. This is because the health risks associated with chemical hazards (e.g. pesticides and polycyclic aromatic hydrocarbons) are often a result of chronic or high levels of exposure that are not likely to occur via recreational activities due to dilution and limited durations of exposure (12).

Toxins released by cyanobacteria can adversely affect health through dermal contact or accidental ingestion or aspiration of water (12). In Moreton Bay, regular annual blooms of the nuisance and potentially harmful cyanobacterium Lyngbya majuscula have been studied extensively (17, 33). Several key toxins have been isolated and characterised from these blooms and anecdotal evidence of toxic incidents reported; however, only limited epidemiological data are available linking toxins and severe skin symptoms among exposed recreational users coming into contact with blooms (17). Most documented cases of human illness associated with cyanobacterial toxin exposures, however, have been associated with drinking water (12). Health risks from cyanobacterial toxins in recreational waters are likely to increase given the widespread nature of the hazards in combination with rising global temperatures, agricultural nutrient run-off and population growth (34-36).

Perceptions of health risks from chemicals in waterways need to be managed alongside actual health risks. This can present a challenge as illustrated by a recent, locally relevant example. Contamination of waterways (including several sites in Moreton Bay) by a particular group of persistent chemicals known as Per- and poly-fluoroalkyl substances (PFAS) has recently triggered high levels of community concern and regulatory attention (37, 38). A recent accidental release of these chemicals via a spill of firefighting foam by an airline into Moreton Bay, along with historical, long-term industrial/commercial use of PFAS has led to potential exposure routes being identified and public health advisories being released (37). Factors such as involuntary, past exposures for particular affected communities via contaminated groundwater, high levels of ongoing media coverage, scientific complexity and uncertainty about long-term health effects have all contributed to elevated levels of perceived risk (38).

In contrast to the psychological risks posed by concerns generated by contaminants entering waterways, ‘blue’ environments can be a key contributor to people’s psychological wellbeing (9, 20). For example, research from New Zealand has shown that higher levels of blue space visibility within a person’s local urban area is associated with lower psychological distress (39). Further, non-coastal blue spaces, such as rivers, have also been shown to have health-enhancing aspects serving as therapeutic landscapes (20). Research investigating UK census data found that people living closer to the coast were more likely to report a good status of health (4). Given that more than 8 in 10 Australians (85%) live within 50km of the coastline these findings are especially interesting (40). With Brisbane, the Sunshine Coast and the Gold Coast being the major population hubs in south east Queensland (SEQ) (40, 41), coastal lifestyles are clearly valued by residents and research is beginning to emerge about how people interact with and what they value about these landscapes (3, 21). Furthermore, research from the UK  also showed that the positive health effect can be more pronounced in deprived areas (4), indicating that blue environments may serve as an important instrument for tackling health inequalities. Urban blue environments may be of critical importance for buffering the stress- inducing characteristics of city living and living in areas of socio-economic disadvantage. Programs for place-based disadvantage in SEQ, such as the ‘Logan Together’ partnership (42), could benefit in the future from more-explicitly nature-based interventions. Water environments such as riverside parks, lakeside trails and beaches provide important settings for people to come together with family, friends and neighbours or as part of larger organised community events. This is evident by the number of popular waterway themed festivals and events that occur in both SEQ (e.g. Riverfire in Brisbane, Lines in the Sand festival on North Stradbroke Island) and across Australia.

Degraded blue environments can negatively impact a person’s sense of wellbeing by causing distress or creating a sense of loss (2, 6). This environmental distress, also termed solastalgia, is produced by environmental change impacting on people while they are directly connected to their home environment (19). As waterways face increasing pressures, signs of degradation can become more obvious and frequent. It is therefore likely that communities that witness algal blooms, fish kills, pollution of their local water environments or climate change impacts may be vulnerable to solastalgia. Similarly, communities may lament over the loss of coastal ecosystems to land reclamation works, canal estate developments and rising sea levels. As traditional custodians of the land, Indigenous communities in Moreton Bay are particularly vulnerable to experiencing a strong sense of personal loss in the face of environmental degradation (43). Once waterways become degraded it can also deter people from visiting and valuing them, decreasing their opportunities for social interaction.

Conceptual frameworks for managing waterways for health

Environmental health, as a discipline, recognises the importance of quality physical environments in protecting health and promoting wellbeing. Moreover, it recognises the complex, reciprocal relationships between human and ecosystem health and advocates for policies that aim to achieve the ‘double dividend’ of enhanced ecosystem services and improved health outcomes (1). The development of effective policies and interventions in this cross-sectoral domain, however, is often constrained by factors such as segregated governance structures and inadequate linkage across sectors of the abundant data being routinely collected about natural resources, planning, environmental management, health and social services. This ‘Data Rich, Information Poor Syndrome’ (DRIPS) was recognised by intergovernmental agencies around the time that the milestone United Nations Conference on Environment and Development was held in Rio de Janeiro in 1992. Two integrative frameworks were developed to evaluate and track environmental performance and to connect measured changes in environmental quality with their causes and consequences. The development and adoption of the DPSIR (Driver, Pressure, State, Impact, Response) framework was promulgated by the Organisation for Economic Cooperation and Development (OECD) (44), while the DPSEEA (Driving force, Pressure, State, Exposure, Effect, Action) framework, was developed jointly by the World Health Organization, The United Nations Environment Program and the United States Environmental Protection Agency to make the pathways between environmental changes and human health outcomes more explicit (45). Both frameworks are designed to facilitate decision-making that considers not only the ‘higher order’ or distal determinants of environmental quality, but pathways through which society is impacted by enhanced or degraded environments. Bowen et al. (46) present a thorough overview and comparison of the DPSIR and DPSEEA frameworks, using international case studies to highlight their differences. Scotland’s Good Places, Better Health Policy initiative in 2008 is featured as the most wide-ranging and inclusive case that shows the value of the DPSEEA framework as an auditing and communication tool among a broad range of policy constituencies and stakeholder groups (46).

Metrics or scorecards can be useful to monitor and communicate the effectiveness of our investments in waterway management. An important caveat here is that rigour around what we are actually measuring with such metrics is critical, as any deficiencies can easily be carried through to oversimplified, but popular messaging. In SEQ, the ecological condition of waterways has been assessed and rated through the internationally acclaimed Ecosystem Health Monitoring Program (EHMP) coordinated by Healthy Land and Water since 2000 (47). An overall Environmental Condition Grade (A–F) is assigned to each of 18 catchments based on a synthesis of 25 indicators reflecting key freshwater and estuarine aspects of the waterways. In response to the need to develop additional metrics to capture the social and economic values associated with waterways, the 5-star Waterways Benefits Rating was developed by Healthy Land and Water and added to the annual report cards in 2015 (47). The 1–5 star rating is based on the following six components:

  1. Community satisfaction with local waterways
  2. Appropriate access to local waterways
  3. Personal benefits residents derive from using local waterways
  4. Community motivation to use and protect waterways
  5. Economic benefits generated through recreation
  6. Contribution relevant catchments make to providing clean low-cost drinking water.

This Waterways Benefits Rating is designed to gather data that would help us better understand how social and economic benefits may be affected by changing environmental conditions; however, it has some shortcomings with respect to capturing the inherent and complex linkages between humans and ecosystems being discussed in this paper.

The DPSEEA framework offers an alternative, more robust approach to the development of metrics that link environmental conditions with human health and wellbeing within Moreton Bay. The first three elements (Drivers, Pressures, State) share perspectives with environmental protection and the protection of water-based ecosystems. This includes the large-scale social Drivers that lead to Pressures that can alter environmental State conditions. The framework then brings in the public health perspective by linking changes in the State of the waterways to Exposure routes and health Effects. The example illustrated in Figure 2 shows how the DPSEEA framework captures some of the links between environmental conditions and health in recreational waters that could be applied to Moreton Bay. Figure 2 also provides examples of metrics that could be monitored as indicators of changes over time. Drivers include population growth, changing land uses, as well as global patterns of energy use and climate change. For the Driver of population growth, another metric could be the proportion of Queensland’s population growth that is concentrated in SEQ (88.3% in 2016–17) (48). A significant amount of research has focused on both climate change impacts and adaptation strategies in southeast Queensland, including numerous projects under the auspices of the South East Queensland Climate Adaptation Research initiative (49). Metrics of Pressures could include sediment inputs due to bank erosion (influenced by land use) and sewage overflows triggered by extreme weather events within an undersized, aging sewerage infrastructure. To assess any changes to the condition of the recreational waterways, State indicators (i.e. observable and measurable measures of water quality such as those metrics incorporated into the EHMP and levels of faecal contamination) should be regularly monitored at the recreational water sites. The Exposure element of the DPSEEA framework is designed to capture how people are exposed to the ‘State of the environment’ variables (e.g. water quality) that impact on their health and wellbeing status (Effect). Bowen et al. describe the Exposure attribute as one that reflects the ‘vectors of risk exposure (either risk elevation or diminution) that emerge as a consequence of environmental change’, and Effect as a measure ‘of change in health resulting from changes in risk exposure’ (46).

While these definitions cater for both the positive and negative linkages between environmental quality and public health, in practice there is a paucity of routinely collected data that could be used for reliable Exposure or health (Effect) metrics. If we wanted to focus on health risks of recreational Exposures, biomarkers could be used to indicate exposure and models could be used to estimate likely numbers of pathogens ingested by recreational water users; however, these approaches are usually only applied in site-specific health risk investigations. On the other hand, focusing on the health-promoting exposures brings additional challenges, as reported benefits are typically narrative. To capture information on both health risks and benefits, it would therefore be best to combine metrics derived from measurements, where applicable, with stakeholder narratives to gain a more holistic understanding of the linkages. This approach is espoused by Waltner-Toews & Kay (50).

The 5-star Waterways Benefits Rating incorporated into the Healthy Land and Water annual report card brings us one step closer to capturing these positive benefits within Moreton Bay and its catchments. Unfortunately, neither the environmental State data relevant to public health (e.g. faecal indicator monitoring) nor the perceived benefits data (e.g. Waterways Benefits Rating) can be geo-referenced directly to EHMP monitoring sites. Using integrated frameworks such as DPSEEA could help us get the best value out of our ecosystem health monitoring and modelling efforts in Moreton Bay by shedding light on the structure of the complex interrelationships between human and ecosystem health.

Figure 2. An illustration of how the Driving force, Pressure, State, Exposure, Effect, Action (DPSEEA) framework can be applied to the management of recreational waters.

The Action element of the DPSEEA framework captures the potential for multi-tiered management responses aimed at improving environmental and health conditions. A unique strength is that it shows how Actions can target multiple points in the DPSEEA pathway and be coordinated across policy sectors. It also facilitates the consideration and integration of more progressive, holistic management strategies such as health-based targets for drinking water management (51), water-sensitive urban design (52) and effects-based management (48, 53). The benefit of these strategies is that they shift environmental management from a regulator-driven, compliance approach to an environmental and community values-driven approach. This does not preclude using traditional tools such as zoning reviews, impact assessments, riparian zone restoration programs, environmental licensing regulations, health protection actions, and policy and clinical responses to the health outcomes. The merits and practicalities of using these approaches in Moreton Bay are currently being explored by a range of stakeholders, including water utilities, councils, researchers and consultants.

Integrative frameworks such as DPSEEA are designed to capture the complexity of the systems they represent. For example, a network of linkages is more likely to represent an issue of concern in Moreton Bay among a mixed group of stakeholders than a single cause–effect pathway. Importantly, DPSEEA can and should be applied flexibly and the stakeholders can begin to populate the elements of the framework from different starting points to promote a better, shared understanding of the integrity of the system as a whole.

Health effects too, are not limited to ill-health and an ongoing challenge when investing in ‘livability’ within catchments is how to capture the positive health and wellbeing contribution of our waterways. Several research projects in Moreton Bay are collecting valuable, in-depth empirical data that could populate parts of the DPSEEA framework. For example, several investigative approaches (microbial source tracking, epidemiological and quantitative microbial risk modelling) are being used by Kozak et al. to better characterise the potential health risks associated with exposure to diffuse and point-source polluted recreational waters (54, 55). Another project by Cleary et al. seeks to understand the role that ‘nature connection’ (the feelings, beliefs and behaviours that people have towards nature) plays in supporting mental health and wellbeing (56).

Variants of this particular conceptual model continue to evolve as our understanding grows. For example, the eDPSEEA (‘ecosystem enriched DPSEEA’) model, developed by Reis et al., extends the State element to incorporate the State of the ecosystem services, as well as positive and negative feedbacks between a wide range of the model’s components. Using eDPSEEA facilitated better engagement with stakeholders and drew out the wider potential implications of reduced amenity on human wellbeing (57).

Conclusions

In striving for improved health outcomes and ecosystem services in Moreton Bay, we will inevitably come up against trade-offs or paradoxes. We need to better understand the science and social values behind these paradoxes to improve the alignment of environmental and public health strategies in order to maximise the gains from both public and private investment in them. Framing complex environmental health issues in Moreton Bay using models such as DPSEEA would provide the backbone of a more rigorous approach for linking existing data, identifying gaps and collecting relevant additional evidence to facilitate more effective actions at multiple levels and across several policy sectors. Combining emerging scientific tools and technologies with the narratives of stakeholders offers exciting new avenues to guide adaptive strategic management of Moreton Bay. The double-dividend of enhanced ecosystem services and improved human health outcomes is a worthwhile goal.

[1] Wetlands are defined broadly by the Ramsar Convention on Wetlands to include rivers, lakes, marshes, rice fields and coastal areas (6).

 

References

  1. Horwitz P, Finlayson M. 2011. Wetlands as settings for human health: Incorporating ecosystem services and health impact assessment into water resource management. BioSciences. 61(9):678-688. http://dx.doi.org/10.1525/bio.2011.61.9.6
  2. Bartram J (Ed). 2015. Routledge handbook of water and health. Baum R, Coclanis PA, Gute DM, Kay D, McFadyen S, Pond K, Robertson W, Rouse MJ, (Eds). Routledge, London & New York. 732 pp. 1317436997.
  3. Cleary A, Fielding KS, Bell SL, Murray Z, Roiko A. 2017. Exploring potential mechanisms involved in the relationship between eudaimonic wellbeing and nature connection. Landscape and Urban Planning. 158:119-128
  4. Wheeler BW, White M, Stahl-Timmins W, Depledge MH. 2012. Does living by the coast improve health and wellbeing? Health & Place. 18(5):1198-1201
  5. Reid W, Mooney H, Cropper A, Capistrano D, Carpenter S, Chopra K, Dasgupta P, Dietz T, Duraiappah A, Hassan R. 2005. Millennium ecosystem assessment. Ecosystems and human well-being: Synthesis. Washington, DC. https://www.wri.org/publication/millennium-ecosystem-assessment-0
  6. Finlayson CM, Horwitz P. 2015. Wetlands as settings for human health—the benefits and the paradox. In: Horwitz P, Weinstein P, Finlayson CM (Eds). Wetlands and Human Health. Springer-Verlag London Ltd, Dordrecht. p. 1-14. http://dx.doi.org/10.1007/978-94-017-9609-5_1
  7. Comberti C, Thornton TF, Wyllie de Echeverria V, Patterson T. 2015. Ecosystem services or services to ecosystems? Valuing cultivation and reciprocal relationships between humans and ecosystems. Global Environmental Change. 34:247-262. https://doi.org/10.1016/j.gloenvcha.2015.07.007
  8. Horwitz P, Finlayson CM, Weinstein P. 2012. Healthy wetlands, healthy people: A review of wetlands and human health interactions. Ramsar Technical Report No. 6. Secretariat of the Ramsar Convention on Wetlands, Gland, Switzerland, & The World Health Organization, Geneva, Switzerland
  9. White M, Bell S, Elliot LR, Jenkin R, Wheeler RW, De Pledge MH. 2016. The health benefits of blue exercise in the UK. In: Barton J, Bragg R, Wood C, Pretty J. (Eds). Green exercise: Linking nature, health and well-being. Routledge in association with GSE Research. p. 69-78
  10. US Environmental Protection Agency. 2012. Recreational water quality criteria. Health and Ecological Criteria Division, Office of Science and Technology, United States Environmental Protection Agency.
  11. Wade TJ, Calderon RL, Sams E, Beach M, Brenner KP, Williams AH, Dufour AP. 2006. Rapidly measured indicators of recreational water quality are predictive of swimming-associated gastrointestinal illness. Environmental Health Perspectives. 114(1):24-28
  12. National Health and Medical Research Council. 2008. Guidelines for managing risks in recreational water. Australian Government.
  13. Coutts AM, Tapper NJ, Beringer J, Loughnan M, Demuzere M. 2013. Watering our cities: The capacity for water sensitive urban design to support urban cooling and improve human thermal comfort in the Australian context. Progress in Physical Geography: Earth and Environment. 37(1):2-28. http://dx.doi.org/10.1177/0309133312461032
  14. World Health Organization. 2003. Guidelines for safe recreational water environments: Coastal and fresh waters. World Health Organization. Geneva
  15. World Health Organization. 2006. Guidelines for safe recreational water environments. Volume 2, swimming pools and similar environments. World Health Organization. Geneva
  16. Weinstein P, Woodward A. 2005. Ecology, climate, and campylobacteriosis in New Zealand. In: Ebi KL, Smith JB, Burton I (Eds.). Integration of public health with adaptation to climate change: Lessons learned and new directions. Taylor & Francis, Leiden. p. 60-71
  17. Osborne N, Shaw G, Webb P. 2007. Health effects of recreational exposure to Moreton Bay, Australia waters during a Lyngbya majuscula bloom. Environment International. 33(3):309-314. http://dx.doi.org/10.1016/j.envint.2006.10.011
  18. Horwitz P, Roiko A. 2015. Ecosystem approaches to human exposures to pollutants and toxicants in wetlands: Examples, dilemmas and alternatives. In: Finlayson CM, Horwitz P, Weinstein P (Eds.). Wetlands and human health. Springer Netherlands, Dordrecht. p. 75-94. http://dx.doi.org/10.1007/978-94-017-9609-5_5
  19. Albrecht G, Sartore G-M, Connor L, Higginbotham N, Freeman S, Kelly B, Stain H, Tonna A, Pollard G. 2007. Solastalgia: The distress caused by environmental change. Australasian Psychiatry. 15(S1):S95-S98. http://dx.doi.org/10.1080/10398560701701288
  20. Völker S, Kistemann T. 2013. “I’m always entirely happy when I’m here!” Urban blue enhancing human health and well-being in Cologne and Düsseldorf, Germany. Social Science & Medicine. 78:113-124
  21. Jones NA, Ross H, Shaw S, Witt K, Pinner B, Rissik D. 2016. Values towards waterways in south east Queensland: Why people care. Marine Policy. 71:121-131. https://doi.org/10.1016/j.marpol.2016.05.027
  22. Queensland Government. 2014. Prefeasibility investigation into flood mitigation storage infrastructure report for the Brisbane River catchment. Department of Energy and Water Supply. Queensland. https://www.dews.qld.gov.au/__data/assets/pdf_file/0005/233438/prefeasibility-investigation-flood-mitigation.pdf
  23. Lundy L, Wade R. 2011. Integrating sciences to sustain urban ecosystem services. Progress in Physical Geography: Earth & Environment. 35(5):653-669. http://dx.doi.org/10.1177/0309133311422464
  24. Schoen ME, Ashbolt NJ. 2010. Assessing pathogen risk to swimmers at non-sewage impacted recreational beaches. Environmental Science & Technology. 44(7):2286-2291
  25. Soller JA, Bartrand T, Ashbolt NJ, Ravenscroft J, Wade TJ. 2010. Estimating the primary etiologic agents in recreational freshwaters impacted by human sources of faecal contamination. Water Research. 44(16):4736-4747
  26. Healthy Land and Water. 2014. Microbial trigger value justification paper. Brisbane, Australia. https://hlw.org.au/resources/
  27. Healthy Land and Water. 2017. Healthy waterplay. [Accessed: 21/09/2018. Available from: http://hlw.org.au/initiatives/healthy-waterplay-sad-14727.
  28. Brisbane City Council. 2018. Water quality monitoring. [Accessed: 17/09/2018. Available from: https://www.Brisbane.qld.gov.au/environment-waste/water/water-quality-monitoring.
  29. Beale DJ, Karpe AV, Ahmed W, Cook S, Morrison PD, Staley C, Sadowsky MJ, Palombo EA. 2017. A community multi-omics approach towards the assessment of surface water quality in an urban river system. International Journal of Environmental Research & Public Health. 14(3):303. http://dx.doi.org/10.3390/ijerph14030303
  30. Garcia-Armisen T, Inceoğlu Ö, Ouattara N, Anzil A, A Verbanck M, Brion N, Servais P. 2014. Seasonal variations and resilience of bacterial communities in a sewage polluted urban river. PLoS ONE. 9(3):e92579. http://dx.doi.org/10.1371/journal.pone.0092579
  31. Korajkic A, Parfrey LW, McMinn BR, Baeza YV, Van Teuren W, Knight R, Shanks OC. 2015. Changes in bacterial and eukaryotic communities during sewage decomposition in Mississippi River water. Water Research. 69:30-39. https://doi.org/10.1016/j.watres.2014.11.003
  32. Langley A. 2004. Risk assessment. In: Cromar N, Cameron S, Fallowfield H (Eds.). Environmental heath in Australia and New Zealand. Oxford University Press, Melbourne. p. 92-110
  33. Hanington P, Rose A, Johnstone R. 2016. The potential of benthic iron and phosphorus fluxes to support the growth of a bloom forming toxic cyanobacterium Lyngbya majuscula, Moreton Bay, Australia. Marine and Freshwater Research. 67(12):1918-1927. https://doi.org/10.1071/MF15219
  34. Kokociński M, Dziga D, Spoof L, Stefaniak K, Jurczak T, Mankiewicz-Boczek J, Meriluoto J. 2009. First report of the cyanobacterial toxin cylindrospermopsin in the shallow, eutrophic lakes of western Poland. Chemosphere. 74(5):669-675
  35. Poniedziałek B, Rzymski P, Kokociński M. 2012. Cylindrospermopsin: Water-linked potential threat to human health in Europe. Environmental Toxicology and Pharmacology. 34(3):651-660
  36. National Health and Medical Research Council. 2011. Australian drinking water guidelines 6. Australian Government.
  37. Australian Government Department of Health. 2018. Per- and poly-fluoroalkyl substances (PFAS). [Accessed: 09/11/18. Available from: http://www.health.gov.au/internet/main/publishing.nsf/Content/ohp-pfas.htm.
  38. Buckley N, Sim M, Douglas K, Hakansson H. 2018. Expert health panel for per- and poly-fluoroalkyl substances (PFAS). In: Department of Health AG, editor. Australian Government. Australia
  39. Nutsford D, Pearson AL, Kingham S, Reitsma F. 2016. Residential exposure to visible blue space (but not green space) associated with lower psychological distress in a capital city. Health & Place. 39:70-78
  40. Department of Infrastructure Local Government and Planning. 2017. ShapingSEQ: South East Queensland Regional Plan 2017.
  41. Roiko A, Mangoyana RB, McFallan S, Carter RW, Oliver J, Smith TF. 2012. Socio-economic trends and climate change adaptation: The case of south east Queensland. Australasian Journal of Environmental Management. 19(1):35-50. http://dx.doi.org/10.1080/14486563.2011.646754
  42. Hogan D. 2017. The state of Logan’s children and families: Final report on child health and wellbeing in Logan, Queensland. Logan Together. Meadowbrook, Qld. http://Logantogether.org.au/wp-content/uploads/2017/09/The-State-of-Logans-Children-Families-V3-reduced.pdf
  43. Pinner B, Ross H, Jones N, Babidge S, Shaw S, Witt K, Rissik D. 2019. Values towards waterways in south east Queensland: Indigenous perspectives. In: Tibbetts, I.R., Rothlisberg, P.C., Neil, D.T., Homburg, T.A., Brewer, D.T., & Arthington, A.H. (Eds). Moreton Bay Quandamooka & Catchment: Past, present & future. The Moreton Bay Foundation, Brisbane, Australia. Available from: https://moretonbayfoundation.org/
  44. OECD. 1993. OECD core set of indicators for environmental performance reviews: A synthesis report by the group on the state of the environment. Paris
  45. Corvalan C, Briggs D, Kjellstorm T. 1996. Development of environmental health indicators. In: Briggs D, Corvalan C, Nurminen M (Eds). Linkage methods for environment and health analysis: General guidelines. World Health Organisation, Geneva. p. 19-53
  46. Bowen RE, Kress M, Morris G, Rothman DS. 2014. Integrating frameworks to assess human health and well-being in marine environmental systems. In: Bowen RE, Depledge MH, Carlarne CP, Fleming LE (Eds). Oceans and human health: Implications for society and well-being. John Wiley & Sons, Chichester, West Sussex, UK
  47. Healthy Land and Water. 2017. Report card 2017 – methods summary. [Accessed. Available from: http://hlw.org.au/u/lib/cms/report-card-methods_pdf_draftfinal_v2017.pdf.
  48. Ministry for the Environment. 2016. Analysis of efficacy of effects-based planning in relation to the national planning template. New Zealand. http://www.qgso.qld.gov.au/products/reports/pop-growth-highlights-trends-qld/pop-growth-highlights-trends-qld-2018-edn.pdf
  49. McAlister RRJ, Lovelock CE, Smith TF, Choy DL. 2012. Final progress report: The south east Queensland climate change adaptation research initiative. CSIRO. Australia
  50. Waltner-Toews D, Kay J. 2005. The evolution of an ecosystem approach: The diamond schematic and an adaptive methodology for ecosystem sustainability and health. Ecology and Society. 10(1). http://www.ecologyandsociety.org/vol10/iss1/art38/
  51. Water Services Association of Australia. 2015. Manual for the application of health-based targets for drinking water safety (v1.2)
  52. Healthy Land and Water. 2017. Water by design. [Accessed: 2018]. Available from: http://hlw.org.au/initiatives/waterbydesign.
  53. Dela-Cruz J, Pik A, Wearne P. 2017. Risk-based framework for considering waterway health outcomes in strategic land-use planning decisions. In: Office of Environment and Heritage, (Ed.) Office of Environment and Heritage and the Environment Protection Authority, Sydney
  54. Kozak S, Ahmed W, Veal C, Weir MH, Toze S, Stratton H, Roiko A. 2017. Advancing evidence-based management of recreational waters (poster presentation). 29th Annual Scientific Conference of the International Society of Environmental Epidemiology (ISEE); Sydney, Australia.
  55. Ahmed W, Staley C, Kaiser T, Sadowsky MJ, Kozak S, Beale D, Simpson S. 2018. Decay of sewage-associated bacterial communities in fresh and marine environmental waters and sediment. Applied Microbiology and Biotechnology. 102(16):7159-7170. http://dx.doi.org/10.1007/s00253-018-9112-4
  56. Cleary, A., Fielding, K. S., Murray, Z., & Roiko, A. 2018. Predictors of nature connection among urban residents: Assessing the role of childhood and adult nature experiences. Environment and Behavior. November. http://dx.doi.org/10.1177/0013916518811431
  57. Reis S, Morris G, Fleming LE, Beck S, Taylor T, White M, Depledge MH, Steinle S, Sabel CE, Cowie H, Hurley F, Dick JM, Smith RI, Austen M. 2015. Integrating health and environmental impact analysis. Public Health. 129(10):1383-1389. https://doi.org/10.1016/j.puhe.2013.07.006