versión On-line ISSN 1816-7950
versión impresa ISSN 0378-4738
Water SA vol.37 no.5 Pretoria ene. 2011
CE van Ginkel*
Cripsis Environment, 590 20th Avenue, Rietfontein 0084, Pretoria, South Africa
During the past 40 years, eutrophication has become an increasing threat to the usability of South African freshwater resources. Despite legislation moderating the discharge of phosphorus from some wastewater treatment works since the 1980s, eutrophication of freshwater resources is now widespread. Two important consequences are blooms of cyanobacteria, carrying the threat of cyanotoxin contamination, and excessive growth of macrophytes, which clog water-supply structures and reduce the recreational value of aquatic resources. Eutrophication-management options include reduction of phosphorus in detergents, biomanipulation of the food web, accurate prediction of cyanobacterial growth cycles, and mechanical disturbance of the epilimnion. The implementation of adaptive management to deal with eutrophication would ensure the testing and application of the most appropriate methodology to each eutrophic water body. Continued monitoring and reporting of trophic status are essential to establish whether interventions are having any effect.
Keywords: biomanipulation, cyanobacteria, eutrophication, forward prediction, management, low-p detergents, phosphorus, zero-phosphate
Eutrophication is the process of nutrient enrichment and the associated excessive plant growth in water bodies. It is part of the natural ageing process of lakes and is accelerated by human impacts. High nutrient concentrations are the result of cultural and natural influxes of nutrients (Fig. 1).
Cultural eutrophication is related to anthropogenic activities - human, social and economic activities. In theory, this form of eutrophication is controllable, because people can take measures to minimise the impact of their activities. Wellknown impacts of cultural eutrophication include:
Accelerated population growth and associated settlement patterns
Watershed or catchment area alterations, such as dams that are built for water storage to supply increasing population needs
Increased wastewater treatment works discharges
Increased fertiliser applications to increase food production
Intensive farming practices that cause increased nutrientpolluted return flows
Poor agricultural practices, for example when farmers plough and cultivate the riparian zones of water resources
Natural eutrophication is caused by the influx of nutrients from natural sources, including the rocks, soil and other natural features within a catchment area. This type of eutrophication is not reversible or controllable, and will therefore continue slowly and inevitably.
The factors driving eutrophication are high nutrient concentration and stagnation for prolonged periods, with suitable temperature, oxygen concentration and proper light regime. These conditions encourage increased primary growth in the form of algae and macrophytes, culminating in severe blooms and eutrophication or, in extreme cases, a hypertrophic state.
In this paper the current situation regarding eutrophication in South Africa will be assessed and the future challenges facing the country will be identified against a historical background of research and management initiatives. The current reality of the eutrophication situation faced by the country will be outlined, and an account will be given of a number of the more recent initiatives to manage eutrophication, as well as a description of an adaptive management process through which it is proposed that the eutrophication problems be addressed in future.
History of eutrophication research andmanagement in South Africa
The history of eutrophication research and management in South Africa is schematically illustrated in Fig. 2. Numerous studies drew attention to the eutrophication problem in the late 1970s and early 1980s and many eutrophication-management options were suggested (e.g. Toerien, 1977; Walmsley and Butty, 1980; Zohary et al., 1988). An effluent standard of 1 mg/ℓ orthophosphate for wastewater discharges from point sources was therefore promulgated by DWAF on 1 August 1980 (Water, 1988). Note that the 1 mg P/ℓ standard is an effluent discharge standard, not an in-stream or inlake standard. The ameliorating effects of natural in-stream processes are relied upon to act on the discharged effluent and reduce nutrient concentrations to acceptable levels within a river system. Unfortunately, the capacity of in-stream processes to achieve the desired nutrient reduction is often exceeded (Hohls, 1998).
During 1985 the Department of Water Affairs initiated the first eutrophication-focused monitoring programme, which covered the 7 sensitive catchments mentioned in the Government Gazette Notice No. 1567. Unfortunately, the Department of Water Affairs acceded to requests from many of the affected authorities by exempting them for 5 years from compliance with the 1 mg P/ℓ standard (Taylor et al., 1984; Van der Merwe, 1989; Van Ginkel et al., 2001).
During the period 1985 to 1988, the Department of Water Affairs and the CSIR completed an investigation, using the Reservoir Eutrophication Model (REM), to predict the impact of the P-standard on water quality in the sensitive catchments (Grobler and Silberbauer, 1984; Rossouw, 1990). On the basis of these findings the target water quality aimed to control eutrophication was set 'to maintain mean chlorophyll concentrations in the receiving water bodies at such levels that severe nuisance conditions would not occur for more than 20% of the time. This translated into a phosphorus management objective (PMO) or endpoint of maintaining mean total phosphorus concentrations in reservoirs at 130 µg/ℓ P or lower (DWA, 1988; ANON, 1988a; ANON, 1988b).
During the 1990s South African eutrophication-related work focused only on specific impacted areas, for example the Buffalo River Situation Analysis (Van Ginkel et al., 1996). The aim of the Buffalo River study was to understand all the pathways and impacts related to eutrophication within the spe cific catchment areas. During the late 1990s and early 2000s, the Department of Water Affairs and the WRC assessed the shortcomings in eutrophication research and management with a specific focus on the WRC's contribution and the impact of its research (Walmsley, 2000; Harding, 2006; Frost & Sullivan, 2010). The result was a renewed focus on eutrophication-related problems and management options after 2000 (Quayle et al., 2010; Van Ginkel et al., 2009).
Eutrophication reality in South Africa
South Africa's most limiting natural resource is freshwater (Van Ginkel et al., 2001). Thus, the provision of safe and suf ficient drinking water in South Africa relies on the availability of freshwater resources.
From 1985 onward, the Department of Water Affairs focused its monitoring on areas affected by eutrophication through the Trophic Status Project. After the implementation of the National Eutrophication Monitoring Programme (NEMP) in 2002, the Department also began regularly releasing data maps indicating the extent of eutrophication thereby improving the knowledge about eutrophication in South Africa for an increasing number of sites. The classification system for the sampling sites used by the Department of Water Affairs is shown in Table 1.
From Fig. 3 it is clear that South Africa is facing widespread eutrophication-related problems, most of them associated with the larger metropolitan areas and the dams on which these areas rely for their water supplies.
The main reasons for viewing eutrophication of freshwater resources as a serious problem, which threatens our ability to supply sufficient and safe drinking water to an increasing population, are the following accompanying factors:
Production of cyanotoxins and their potential impact on the health of end users
Financial implications of dealing with noxious macrophyte control
Cyanobacterial blooms and their effects are symptoms of increasing eutrophication. They are widespread, frequent and typically seasonal. Many cyanobacterial genera produce one or more of a range of cyanotoxins (WHO, 1999) and many are associated with taste and odour problems encountered by water treatment works (Wnorowski 1992; Swanepoel et al., 2008). The ingestion of water containing high concentrations of cyanobacterial toxin (in drinking or in recreational waters) presents a risk to human and animal health (Pouria et al., 1998; WHO, 1999; Botes et al., 2004). The increasing frequency of cyanobacterial blooms in South African impoundments and rivers is a cause for concern. Since 1990 the research focus, internationally and nationally, has shifted to expanding our knowledge of the driving forces behind cyanobacterial blooms and cyanotoxin production. Toxic cyanobacterial blooms are a threat to the supply of safe drinking water in large parts of South Africa (Van Ginkel, 2004), especially in areas where water purification is minimal or not fully functional (Van Ginkel and Conradie, 2001).
Microcystis spp. are the dominant bloom-forming cyanobacterial species present in South Africa (Wnorowski, 1992; Harding and Paxton, 2001; Downing and Van Ginkel, 2003; Van Ginkel, 2004). Additionally Oscillatoria spp. (Harding and Paxton, 2001, Van Ginkel and Conradie, 2001) and Cylindrospermopsis (Van Ginkel and Conradie, 2001) occur in bloom-forming condition.
Production of cyanobacterial toxins in 5 South African hypertrophic systems is several orders of magnitude higher than figures reported for northern hemisphere countries (Fig. 4 and Fig. 5). The 5 most hypertrophic systems in South Africa have cyanotoxin concentrations in excess of 1 µg/ℓ for more than 80% of the time (Fig. 4). South African maximum total microcystin concentrations are also much higher than those reported in Finland and North America.
The severity of cyanobacterial blooms in South Africa is evident from the number of livestock and wild animal deaths recorded since 1950 (Harding and Paxton, 2001). Eutrophication-related contamination of water also occurs in the Kruger National Park and several mammal deaths were reported during 2005 and 2007 (Oberholster, 2009). Clearly, management techniques aimed at preventing widespread cyanotoxin poisoning need to be applied in South Africa.
Excessive macrophyte growth
The presence of high concentrations of nutrients supports the rapid growth of macrophytes. Excessive macrophyte biomass blocks waterways, impedes access to dams and rivers, clogs drainage systems and contributes to flooding and the destruction of canals.
Water hyacinth (Eichhornia crassipes) control alone costs South Africa in the order of R12 million per annum.
The widespread economic damage is matched by the ecological effects which result in the displacement of indigenous flora and fauna through habitat alteration (Byrne et al., 2010). Many aquatic macrophytes are exotic, problem-causing species, including water hyacinth, red water fern (Azolla spp.), water lettuce (Pistia stratiotes), Kariba weed (Salvinia molesta), Hydrilla (Hydrilla verticillata) and parrot's feather (Myriophyllum aquaticum). Hydrilla is the latest addition to this list of problematic species, although its presence was already recorded in South Africa as early as 1963 (Coetzee et al., 2011b).
Extensive research has been done on the management of these noxious aquatic weeds. Many biological control methods (Cilliers, 1991; Cilliers et al., 2003; Modjadje Vegetation, 2008; Coetzee et al., 2011a) and chemical control methods have been implemented with varying degrees of success. An integrated approach appears to be the most promising solution to combat aquatic weeds, especially water hyacinth (Modjadje Vegetation, 2008; Byrne et al., 2010).
Over the years, it became increasingly apparent that South Africa needs to perform pilot testing of eutrophication-management options to determine their effectiveness and applicability for implementation at other impacted sites. This realisation prompted the initiation of management-focused research through the WRC (Pillay and Buckley, 2001; Rossouw et al., 2008). A number of the more recent case studies that have been or are being conducted to investigate plausible options to manage eutrophication are discussed below.
It is acknowledged that the most effective method to combat nutrient enrichment is to minimise the influx of nutrients into freshwater systems. This perspective prompted the re investigation of means to control the influx of phosphate into water bodies. The first study in this regard was to investigate the desirability of introducing low phosphorus detergents. The WRC consequently commissioned a project entitled 'Investigation of the positive and negative consequences associated with the introduction of zero-phosphate detergents into South Africa', with the main aims of determining:
The contribution of detergent phosphates to the phosphate loading at wastewater treatment facilities
The potential impact of introducing low- to zero-phosphate detergents into South Africa (Quayle et al., 2010).
Impacts of the removal of detergent phosphorus on in-dam phosphate and chlorophyll a levels were modelled based on predicted reductions in inflow loading using the OECD eutrophication model Jones and Lee, 1982) and the Walker Reservoir Models (Thornton and Harding, 2005). Results show a variable decrease in total phosphorus ranging from 3% - 35%, largely dependent on the demographics of each catchment. A mean reduction of 12% across all dams was calculated (Quayle et al., 2010).
Next, a number of dams were studied to determine the potential effect that the introduction of zero-phosphate detergent can be expected to have on the time dams spend in a non-eutrophic state (55 µg/ℓ total phosphorus in-lake median concentration used as a threshold (Harding, 2008)) (Table 2). It is clear that some dams could potentially receive a much lower phosphorus input, especially the most hypertrophic sites. Although this is not the ultimate management option and will not eliminate phosphates from freshwater systems, it is potentially the first important step towards active control of eutrophication in South Africa since the implementation of the 1 mg P/ℓ standard in 1980. Legislation should compel detergent manufacturers to produce low-phosphate or phosphate-free detergents. To promote their use they should be made available at the same cost as detergents containing phosphate. At least one large manufacturer has already undertaken to do this voluntarily (Quayle, 2011).
Biomanipulation techniques target food-chain functioning and involve the use or harvesting of non-desirable organisms to eventually control algal growth or other components of the food chain that may cause eutrophication-related problems. The main aim is to control certain key species at critical points in the food web, e.g. fish species that prey on zooplankton to an extent that may alter the normal functioning of the ecosystem. These methods have been studied extensively in the northern hemisphere, but need to be tested locally in order to evaluate their applicability under South African climatic conditions. The northern hemisphere test sites were in cooler regions with shorter summer seasons than South Africa.
DH Environmental Consulting, funded by the Finnish Government in association with DEA and DWA, developed a management plan for the Hartbeespoort Dam. The Department of Water Affairs continued its support of this initiative by funding a project (Harties, Metsi a Me) on the Hartbeespoort Dam to combat the severe eutrophication impacts in this system. This project is testing an integrated water-management system and is managed by the Regional DWA Office at Hartbeespoort Dam. They are testing methodologies, monitoring quite extensively, harvesting fish and improving upstream wetlands. One of the objectives of the project is to improve the zooplankton concentration. At time of publication the project is ongoing and a final assessment is not available, but preliminary results suggest that the concentration of filter-feeding cladoceran zooplankton increased during the summer period from 2008 to 2010 (Fig. 6).
The efficacy of the eutrophication-management methods used for Hartbeespoort Dam still needs to be confirmed during the final evaluation of the successes and failures of the project in combination with results of the monitoring initiative. For example, evidence is needed to support the hypothesis that the gradual increase of filter-feeding cladoceran zooplankton, specifically during summer, is the result of a greater abundance of the edible algal species preferred by zooplankton present in the system, which in turn came about in response to the manipulation of the food chain by fish harvesting.
Prediction of cyanobacterial blooms
The regular occurrence of cyanobacterial blooms and the potential health hazard posed by cyanotoxin production necessitate the development of forecasting tools. This will enable effective risk management by potable water-treatment works operators and controllers and provide early warning for recreational users. By implementing a forward prediction model to determine cyanobacterial bloom development, a water-treatment works controller will know when to stop pre-chlorination. The release of cyanotoxins into the treated water through die-off of algal cells during the pre-chlorination process is thus prevented (Swanepoel et al., 2008). Forewarning of abnormal conditions also enables a water-treatment process manager to purchase extra supplies, such as the case where activated carbon is not part of the normal treatment procedures.
The WRC funded a study that investigated the effectiveness of different models for forward prediction of cyanobacterial biomass (Van Ginkel et al., 2009). The hybrid evolutionary algorithm method, used to develop a rule-based agent for the forward prediction of Microcystis biomass in hypertrophic reservoirs of South Africa, proved to be the best. Data from Hartbeespoort Dam, Roodeplaat Dam and Rietvlei Dam for the period 1991 to 2005 was used to develop the best algorithms for the forward prediction of Microcystis biomass. The model was trained on 12 years' data from each dam, providing a set of 36 years' combined data for the 3 dams, while setting aside 2 years of data from each dam on which to test the developed algorithm. Thus 6 years of data were available for testing the algorithm (Fig. 7).
Sensitivity analysis indicates that initial biomass (estimated from chlorophyll a) and surface temperature, are the most important environmental variables for the 7-day forward prediction of Microcystis biomass in hypertrophic systems.
Under low phytoplankton-growth conditions the increases in initial biomass and surface temperature are the most important environmental variables contributing to the increase in Microcystis biomass. Under bloom-forming conditions, the increased changes in Microcystis biomass are primarily explained by the total phosphorus concentrations within the system (See Fig. 8).
Epilimnion disturbance through laminar flow
Epilimnion mixing is one of the most appropriate methods of combating cyanobacterial blooms (Hart and Hart, 2006). For this reason, the City of Tshwane, through their Rietvlei Water Treatment Works and in collaboration with the Department of Water Affairs, purchased 6 SolarBee® (patented solar-powered water circulator) pumping units and installed them in Rietvlei Dam in July 2008. The instruments were placed primarily near the intake water inflow into Rietvlei Dam. These instruments cause laminar flow that disturbs the water column to such an extent that conditions become unfavourable for cyanobacterial growth. Another 10 SolarBees were purchased in 2009 and placed in the dam, which is now covered extensively by these 16 devices.
The SolarBees in Rietvlei Dam are set up with the intake hoses at a depth of 4 m in order to cause laminar flow and disturb the stability of the epilimnion. The systems therefore do not cause complete mixing throughout the thermocline. The City of Tshwane is monitoring Rietvlei Dam regularly to assess the effectiveness of the SolarBee® instruments under South African conditions. The WRC is funding a follow-up project to the forward prediction model development, which is testing the model at the Rietvlei Dam Water Treatment Works. According to Coetzee (2011) the phytoplankton community has since installation of the SolarBee® instruments shifted away from the regular annual cyanobacterial blooms.
Adaptive eutrophication management
Various initiatives are under way for managing eutrophica tion in South Africa. The nation's research advisors will need to develop strategies to implement the most effective methods. One way to formalise the process is through adaptive eutrophication management (Fig. 10). Herewith the 6 steps that should be followed for successful adaptive eutrophication management:
Step 1: Monitoring
Monitoring is the first step in combating the problem. If monitoring does not happen, the extent of the problem, or sites in need of management, will not be known. Monitoring the extent of eutrophication in the country should lead to directed research to discover or investigate the most appropriate methods to implement at each impacted site.
Step 2: Directed research
Directed research determines the most effective management options for each specific site. This may be done by investigating all potential management options on small or large scale, leading to a better understanding of the problem. Directed research encourages the development of new monitoring methodology, management, and predictive capabilities, nutrient-limiting approaches and in-lake management options. Preferably, research or investigation of each management option should take place at different localities, to enable prioritisation according to efficiency and financial implications. In this way, management options can be considered in isolation and decisions can be based on scientifically sound research. This process will provide managers with several options to select from, when developing the manage ment plans for a specific site.
Step 3: Develop plans
Next, the selected eutrophication-management plans need to be developed with a view to implementation. An adequate budget is essential for this purpose.
Step 4: Implement plans
Next, the eutrophication-management plans need to be imple mented. Budgeting for sufficient funds is the sole responsibility of the national, regional and local institutions.
Step 5: Monitor successes
The functioning of implemented plans needs to be monitored and reported on in order to determine their effectiveness. When successes and failures are monitored and documented well, decisions to adapt management plans should fall in place.
Step 6: Adapt plans
The management plans need to be adapted, if necessary. Adaptation aligned to the outcome of implementation monitoring should ensure that the necessary funding is available for implementing the adapted implementation plans.
The responsibility to manage eutrophication in South Africa lies with the national, regional and local management institutions. In addition to the measures outlined in Steps 2, 3, 5 and 6, research institutions at national, regional and local levels should apply their knowledge in order to assist and improve eutrophication management in South Africa.
By following these 6 steps, South African water-resource managers can select the appropriate eutrophication-management strategy for each impacted site. This pre-empts crisis control. Sustainable management plans can be implemented to ensure safe water and accessible recreational sites to all end users.
Many control methods have been suggested and tested internationally:
Flow augmentation or flushing
Selective removal of hypolimnetic water
Laminar epilimnion disturbance
Covering bottom sediment
Research on the effectiveness and applicability of these different methods in South Africa is critically important. The results will assist in selecting eutrophication-control measures suitable for South African climatic and economic conditions, in order to reach the ultimate goal of combating eutrophication sustainably in South African inland waters.
Eutrophication is a serious problem in a number of catchment areas in South Africa which appears to have escalated over time. The root of the problem is nutrient enrichment in freshwater resources and therefore the most important management approach involves minimising the influx of nutrients into freshwater systems. However, this approach is being supplemented with several other methods that are currently being evaluated or have been assessed in the recent past. The contributions of the Water Research Commission, the Department of Water Affairs, the CSIR, and their co-workers have been fundamental in creating the substantial knowledge base that already exists. Integrated water resource management for eutrophication should include:
Continued monitoring programmes
Continued initiatives to reduce the release of phosphorus into water resources; e.g. by introducing the use of low-P detergents
The development of a knowledge base encompassing all efficient and viable eutrophication-management options for
South African climatic conditions and social requirements
In-lake management options for sites that are already hypertrophic
Consideration of the further implementation of effective eutrophication-management methods to be used at further impacted sites
Ensuring adequate funding and efficient expenditure to combat the problem of nutrient enrichment of freshwater resources in a sustainable manner.
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This paper was originally presented at the Water Research Commission 40-Year Celebration Conference, Kempton Park, 31 August - 1 September 2011.
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