- freely available
Int. J. Environ. Res. Public Health 2012, 9(10), 3484-3505; doi:10.3390/ijerph9103484
Abstract: The Hartbeespoort (HBP) Dam is a reservoir used for agricultural, domestic supply of raw potable water and recreational activities in South Africa’s North-West Province. Eutrophication and cyanobacterial blooms have long been a cause of water-quality problems in this reservoir. The most prevalent bloom-forming species is Microcystis aeruginosa, often producing the toxin microcystin, a hepatotoxin which can negatively impact aquatic animal and human health, and poses a problem for potable water supply. Algal samples were collected monthly from four pre-determined sites in the dam during the summer months (December 2010–March 2011). Intracellular microcystins (MCs) were extracted using SPE C18 cartridges, followed by separation, identification and quantification using LC-ESI-MS techniques. Quantitative variation studies of MCs were conducted with respect to MC congener isolated, sampling site and month. Three main MC congeners (MC-RR, -LR and-YR) were isolated, identified and quantified. In addition, three minor MCs (MC-WR, MC-(H4)YR and (D-Asp3, Dha7)MC-RR were also identified, but were not quantified. The MC dominance followed the order MC-RR>MC-LR>MC-YR across all sites and time. The maximum and minimum concentrations were 268 µg/g and 0.14 µg/g DW for MC-RR and MC-YR, respectively, of the total MCs quantified from this study. One-way ANOVA showed that there were no significant differences between average MC concentrations recorded across months (P = 0.62), there was, however, a marginally-significant difference in concentrations among MC congeners (P = 0.06). ANCOVA revealed a highly significant interaction between sites and MC congeners on MC concentration (P < 0.001).
Hartbeespoort Dam is situated in the North-West Province of South Africa. The reservoir is fed by the waters of the Crocodile and Magalies Rivers (Figure 1) and has a mean depth of 9.6 m, maximum depth of 45.1 m and surface area of 20 km2. Hartbeespoort Dam is renowned for its poor water quality and is arguably one of the World’s worst examples of eutrophication, due to the high nutrient loads which enter the system and have overburdened the reservoir basin for decades.
Microcystins (MCs), a group of cyclic heptapeptide hepatotoxins are produced by a number of cyanobacterial genera [1,2]. Freshwater microcystin-producing cyanobacterial species, including Microcystis spp., Anabaena spp., Planktothrix (Oscillatoria) spp., Aphanizomenon spp. and Nostoc spp. [1,2], are on the increase worldwide due to increased environmental and water pollution leading to eutrophication of aquatic environments [1,2,3,4,5]. Microcystins are characterised by the presence of a unique non-proteinogenic β-amino acid called ADDA [6,7,8,9]. The toxicity of MCs is highly dependent on the ADDA group, the MeDha group (MeDha = N-methyldehydroalanine) and the structural cyclic nature [10,11]. Over 80 known microcystin structures (variants) have been reported worldwide from freshwater systems with their variations being mainly due to amino-acid replacements either at position 2 or 4 of the MC backbone , for details on the general structure refer to Sivonen et al. . Other structural variations have been attributed to methylation/or demethylation processes of the methyl groups on amino acids at positions 3 and/or 7 [7,8]. The ADDA group  is highly conserved in microcystins (and nodularins) and stable against physiological replacements by other amino acids. Due to this stability, the ADDA group has therefore been utilised in various methods for the identification of microcystins (and nodularins) as described in Msagati et al. , these include ELISA , HPLC-UV/PDA [15,16,17,18,19], LC-ESI-MS [18,19], etc. In positive mode LC-ESI-MS the ADDA group gives a characteristic fragment ion at m/z 135 corresponding to the [phenyl-CH2CH(OCH3)]+ ion . This ion therefore is often used as a diagnostic feature for the identification of MCs in algal samples [13,18] when using the LC-ESI-MS technique. The LC-MS technique gives reliable data with regard to detection, identification, quantification, differentiation and discovery of new MC congeners than other methods stated above . For instance, it has been observed that ELISA is prone to cross-reactivity with MCs other than the MC-LR variant and thus its use is limited whenever identification and quantification of specific MC variants in samples is necessary [21,22,23,24,25]. However, the LC-MS offers complementary results for accurate detection and quantification of the same [7,18].
Cyanobacterial cell deaths caused by ageing, stress, mechanical breakdown or chemical activities (e.g., grazing, water purification processes, pump suctions, boat propellers, etc.) result in releases of intracellular MCs and increased extracellular MCs into the surrounding water [26,27,28,29,30]. Extracellular MCs are both highly soluble and relatively stable in water  posing a worldwide health concern. Microcystin toxicities resulting in human illnesses, as well as wildlife and fish kills, have been reported [2,3,10,17,32,33,34,35,36,37], including many cases in South Africa . The characteristic solubility of MCs in water therefore makes these toxins bioavailable for a couple of days in a water column [23,31] before they can be completely biodegraded. The accumulation of MCs in marine organisms , aquatic plants and other life forms found in water environments [23,40,41,42] has been reported.
Microcystin loading and spatial distribution in a given aquatic ecosystem is a function of intracellular MC content in algal cells and is closely related to algal species dynamics and dominance . Papadimitriou et al.  showed that extracellular MC concentrations extracted from water samples were lower than intracellular MC concentrations extracted from algal cells collected from the same location and time, indicating dangers of possible underestimation or overestimation of MC concentrations should quantification be based solely on extracellular MCs. Lower estimates in extracellular MC levels compared to total intracellular MC levels are due to a number of factors, including algae grazers , assimilation of bioavailable MCs by aquatic organisms, wash-away by water drifts, adsorption on suspended solids/organic matter/sediments, MC degradations , etc. Thus, depending on the method used, measuring intracellular MC concentrations gives more complete information on the quantity and type of MCs, species distribution and their dynamics rather than using extracellular MC concentrations .Seasonal and temporal variations in cyanobacteria population, particularly with M. aeruginosa dominance in Hartbeespoort Dam, have been studied [24,38,46,47,48] and shown to be related to MC production as described elsewhere [29,43,49]. However, to the best of our knowledge and based on the literature surveyed, little information exists in terms of quantitative assessment of intracellular MC with respect to congener concentration variations, dominance and distribution in the Hartbeespoort Dam. In terms of quantitative studies on MCs commissioned and funded by the Water Research Commission (WRC), South Africa (www.wrc.org.za), including some recent works, the results presented were mainly based on total microcystin concentrations expressed as MC-LR equivalence using immunoassay or biochemical methods [25,50]. However, Conti et al.  demonstrated that besides immunoassay/biochemical methods being very sensitive tools for MC detection and quantification, their use results in over-estimations of toxins, probably due to cross-reactivity, false positives or false negatives [22,40,52,53,54,55]. Therefore, the objectives of the present study were to:
Extract and identify intracellular microcystin congeners from algal blooms collected from four sites on the dam accessible by the public either directly or indirectly (by boat).
Quantify intracellular microcystin congeners using the LC-ESI-MS technique and determine their spatial distribution with respect to locations (sites), time and MC type (congener).
Establish an MC congener dominance profile for water-quality assessment with respect to the use of Hartbeespoort Dam water resources.
2. Materials and Methods
2.1. Sample Collection
Samples were collected monthly from December 2010 to March 2011 from four pre-determined sites in the Hartbeespoort Dam (Figure 1), based on four factors:
Areas that can easily be reached either by boat or by walking along the banks of the dam (S1–S4).
Relative distance to fishing/conservation area hotspots (S2–S4).
Proximity to Magalies River inflow and Crocodile River outflow to/from the dam (S3 and S1, respectively).
Proximity to the animal conservation area (zoo) and water purification station (S1).
Algal cells were collected in 500 mL glass bottles from each site during the summer season. Samples were transported to the laboratory in cooler boxes filled with ice blocks and processed the same day by filtration. For algal identifications, samples were treated according to [56,57] and analysed within 24 h of collection.
2.2. Sample Pre-Treatment for Microcystin Extraction
Algal cells were filtered on pre-weighed GF/C glass-fibre filters (47 mm, 0.45 µM). Filters were washed further by flushing with distilled water to remove any superficial microcystins remaining on cells. Filters were stored at −20 °C before freeze-drying. After freeze-drying, weighed algal cells (1.0 g) were extracted using 70% MeOH(aq) and then the extracts were subjected to CHCl3/MeOH/H2O liquid-partitioning (7/6/3, v/v/v) to remove pigments, co-eluting compounds and other cartridge-blocking material  prior to SPE extraction using WatersTM HLB cartridges .
2.3. Physicochemical Parameters and Species Identification
On-site physicochemical parameters (conductivity, temperature, pH and dissolved oxygen) were measured immediately at each site using multifunction meter (YSITM 6-Series Sonde, Marion, Germany). The determination of the concentrations of chlorophyll-a, nitrates and phosphates as well as species identification were carried out in a parallel project that dealt with the assessment of nutrient loading in the Hartbeespoort Dam (Zoology Department, University of Johannesburg).
2.4. Analytical Standards, Reagents and Laboratory Materials
Organic solvents (MeOH, CHCl3, MeCN, HCOOH) were of high purity analytical grade and/or HPLC grade, >99% purchased from Merck (Johannesburg, South Africa) and/or Alfa Aesar (Karlsruhe, Germany). Microcystin standards (MC-RR, -YR and -LR) were purchased from CyanoBiotech GmbH (Berlin, Germany) and were supplied by Industrial Analytical (Pty) Ltd (Johannesburg, South Africa). SPE cartridges (Waters OasisTM HLB cartridge: 60 g, 3 mL) were purchased from Waters Inc. (Milford, MA, USA), and supplied by Microsep (Pty) Ltd, SA (Johannesburg, South Africa). Samples were filtered through Whatman GF/C glass-fibre filters (porosity 0.45 µM, Whatman International Ltd., Maidstone, UK).
2.5. LC-ESI-MS Instrumentation and Conditions
The SPE extracts were analysed using a modified method reported in the literature . Briefly, a WatersTM LC-MS instrument (with a WatersTM 3100 Mass Detector) coupled with an electrospray ionisation source (ESI) was conditioned for 10 min with the mobile phase shown below. MCs separation was performed on a conditioned C18 column (Waters Symmetry300TM, 4.6 mm × 75 mm, 3.5 μm) using the Alliance WatersTM e2695 separation module. The mobile phase consisted of a mixture of 0.5% (FA) in Milli-Q water (A) and 100% acetonitrile (B). The column was operated at room temperature, and the microcystins were eluted within a gradient window of 20 min using a reverse phase system consisting of 25% B (10 min), 70% B (10 min), 25% B (11.1 min), 25% B (20 min). Flow rate and sample injection volumes were set at 0.5 mL/min and 0.5 μL, respectively. The ion source was operated on both positive and negative ESI modes for all experiments. Structural identification of microcystins in samples was based on retention time and fragment ion products relative to respective elution window/fragmentation pattern of authentic analytical standards, results were complemented with literature values.
2.6. Microcystin Analysis and Quantification
Reference standard curves were established from linear regression values of respective authentic microcystin standards using SigmaplotTM Software (Version 8). Linear regression equations were established giving acceptable R2 values for each authentic standard solution. Major intracellular microcystins (MC-RR, -YR, and -LR) isolated from M. aeruginosa cells were quantified based on linear regression equations using peak areas [60,61,62]. All experiments on field samples were performed in triplicate and quantities were reported in mean values (n = 3). Statistical analyses (one-way ANOVA and ANCOVA) were performed on an R2.14.1 statistical package  using mean values of the calculated MC concentrations (P < 0.05 denoted a significant difference).
3. Results and Discussion
3.1. Site Selection
The Hartbeespoort Dam (GPS co-ordinates: 25°43'44.56"S, 27°51'30.35"E) is one of the major water impoundments situated in North-West Province, South Africa, with its water being used for irrigation, domestic and recreation purposes . Thus monitoring of the quality of its water is a primary priority for public health. However, on a daily basis, this reservoir receives millions of litres of treated wastewater that is rich in phosphates and nitrogenous species, this has led to excessive nutrient loading resulting in Hartbeespoort Dams being one of the most heavily eutrophied dams in South Africa [65,66]. Eutrophication of this dam dates back to beyond the 1970s and the water is quite often characterised by foul smell and heavy green pigmentation especially during summer seasons . However, substantial lake restoration control measures are currently underway to reduce nutrient loading (phosphorus/nitrogen), and a shoreline restoration project is being undertaken . Physical removal of algae and water hyacinth after trapping them with floating boom barriers is also an ongoing dam-remediation project managed by DWAF . Sample-collection sites were pre-selected in areas where operational dam restoration and sampling activities would not have any effect/impact on each other. However, sample-collection sites were meant to give a large representative sample area of the dam with different features of interest relevant to public health including recreational and fishing activities and unrestricted/ease of public access (Sites S1–S4) (Figure 1). A pre-survey (and during GPS positioning exercise) showed that Site S1 experienced visible algal cell accumulation during the summer, probably due to the wind direction and effects of currents caused by the outflow of water near the water gates. In addition, this site (S1) was situated within a few metres from the water-purification facility for domestic use as well as to the animal conservation area (known as the Snake Park). Site S2 was selected due to low current and turbulence effects that led to massive algal scum throughout sampling. Algal blooms characteristically occur in calm, nutrient-rich water bodies . Likewise, Site S3 was a relatively calm site, and protected from strong winds by some bushes forming part of a conservation scheme around the dam. The water mass around Site S3 is mainly from Magalies River inflow (Figure 1). Persistent small quantities of algal cells are very common around Site S3, even during the winter season (personal communication from a local resident).
3.2. Microcystis spp. Identification
Preserved cells were identified microscopically according to the Utermöhl method as described . Microcystis aeruginosa species was the dominant species throughout the sampling period across all sites with an average dominance rating of over 80% (i.e., 80% to 100% of total cells identified belonged to M. aeruginosa), data not shown. These findings corroborate those reported in other previously published reports which state that over the past two decades M. aeruginosa has been dominant in Hartbeespoort Dam, particularly during the summer season [25,48,50,71,72]. Other algal species identified included M. wesenbergii (<10%), Spirulina (<5%), Planktothrix spp. (<5%), Melosira spp. (<1%) and Nitzschia spp. (<1%). However, although their presence in this dam has been previously reported [25,50,71], none of these minor species have been associated with MC production in Hartbeespoort Dam. Hence it is widely accepted that M. aeruginosa is the major producer of MCs observed in this dam.
3.3. On-Site Environmental Conditions
Some important physicochemical parameters that prevailed in the dam during the summer are shown in Table 1. The proliferation and persistence of M. aeruginosa as well as MC production are dependent on a number of environmental conditions prevailing in any given water body [2,46,73,74,75]. While an increased N:P nutrient ratio is known to be crucial in this regard , other important parameters have previously been demonstrated to play an important role in MC production, including as demonstrated recently, optimal pH and temperature , as well as light intensity [25,75]. During the entire period of our study, the average pH levels in the dam ranged between pH 8.8 ± pH 0.21 to pH 7.4 ± pH 0.07. This pH range is suitable for desolvation of phosphates in a water system as demonstrated by Greenwald . The availability of soluble phosphates in water increases as the pH of the solution increases towards alkaline conditions up to a pH < 8.6 . The optimal pH range observed in Hartbeespoort Dam is a characteristic feature of most eutrophic waters [71,78] as it is suitable for metabolic activity and growth of toxic algae [5,71,75,79] at the expense of less favoured algae. Similar to previously reported pH values [25,38,71], floating algal cells were conspicuous on the water surface throughout the dam, including all sampling sites where M. aeruginosa cells were collected (Figure 1). The presence of larger masses of algal cells in some areas (e.g., Site S1 and Site S2), which were later shown to be dominated by M. aeruginosa, indicated that the dam conditions were favourable for M. aeruginosa growth, distribution and dominance as shown earlier [46,50].
Algal growths were observable throughout sampling dates, during which the average temperature in December 2010 through to March 2011 ranged between 24.2 °C and 26.2 °C (Table 1). The observed temperature range is typical for summer seasons as reported elsewhere favouring the growth of Microcystis spp. [4,28,29,33,73,74,80] as is the case in Hartbeespoort Dam [25,50]. There was an increase in the quantities (>5.94 µg/g DW) of all MCs extracted towards mid-summer, particularly by February 2011 during which period the water surface in the dam was completely green, evidenced by higher quantities of chlorophyll-a measured (data not shown). Algal cell multiplications result in an increased algal biomass paralleled by an increased quantity of chlorophyll-a being produced, as well as elevated MC production [76,81]. Higher quantities of MCs were recorded at Site S2 (Figure 1-Figure 3) where chlorophyll-a concentration was the highest, being higher than S1, S3 and S4 (data not shown). A correlation between higher total MC concentrations expressed as MC-LR eq/L and higher chlorophyll-a concentrations have been reported for algal cells collected from this dam [25,47,50]. Areas around Site S1 and Site S2 have been identified as some of the historical algae concentration zones due to their locations and conditions that favour massive algal cell aggregations and growth .
A decrease in DO is commonly associated with microbial activity taking place . Towards the end of the summer season there was a tremendous decrease in DO across all sites, an indication that there was higher microbial activity, probably due to bacteria feeding on dying algal cells. A decrease in intracellular MCs extracted from all sites (S1 to S4) in March 2011 supports this observation (compare Figure 2 and Table 2). A decrease in intracellular MC towards the end of the summer is of particular importance in terms of public health since higher releases of extracellular MCs are expected due to cell deaths. Decreasing numbers of visible algal cells in a water column and clear water can be a deceiving water-safety indicator to users, should there be no post-bloom monitoring strategies to determine MCs in recreational water as well as in domestic water, particularly after the summer.
3.4. Isolation, Separation and Identification of MCs using LC-ESI-MS
Pooled MC-rich hydroalcoholic extracts from a partitioning step were dried under vacuum at 40 °C, then re-dissolved in 1 mL MeOH and subjected to the SPE protocol . After LC-MS instrument and column conditioning (10 min), retention times (RTs) for pure and mixed standards were established and optimised. Similarly, SPE products of algal samples were injected into the column using the auto-sampler and eluted for 20 min as had been done for the standards. Three major microcystins, namely MC-RR, -YR, -LR and a few minor microcystin variants, namely MC-WR, MC-(H4)YR and (D-Asp3, Dha7)MC-RR were separated and identified based on m/z signals in positive ESI mode. The negative mode did not give good results, so it was not used.
The observed molecular ion masses, fragments and retention times were analysed relative to those of the authentic standards used in this study and compared to the literature values. The assignments were as follows: MC-RR: (m/z 1,039.0 [M+H]+, ADDA m/z 135, RT 6.57), MC-YR: (m/z 1,046.3 [M+H]+, 523.3 [M+2H]2+, ADDA m/z 135, RT 7.54), MC-LR: (m/z 996.3 [M+H]+, ADDA m/z 135, RT 7.75) and MC-WR: (m/z 1,069.3 [M+H]+, ADDA m/z 135, RT 8.37). The ADDA fragment ion [PhCH2CH (OCH3)]+ (m/z 135) resulted from α-cleavage of the methoxy group of the ADDA residue from microcystins [83,84] and was used as a diagnostic fragment for MC identification [13,18,85]. Except for MC-LA (not isolated in this study), our results are therefore in agreement with those of previous studies that reported on the occurrence of M. aeruginosa in Hartbeespoort Dam and the presence of various microcystin congeners including MC-RR, -YR, -LR, -LA and -WR [46,48,86]. From our work, further analysis of LC-ESI-MS data showed two other minor MCs from all algal extracts collected from all sites (December–March), which is also an indication that the species producing these MCs dominates during summer and is well distributed in the whole dam. Structures of the minor MCs corresponded to MC-(H4)YR (m/z 1050, [M +H]+, m/z 135, ADDA)  and (D-Asp3, Dha7) MC-RR (m/z 1010, [M+H]+, m/z 135, ADDA) when compared with information gleaned from the literature . These two MCs (i.e., MC-(H4)YR and (D-Asp3, Dha7)MC-RR) have previously been isolated from M. aeruginosa elsewhere [62,86], but there is limited information on their production from the same species found in the Hartbeespoort Dam, thus more investigation is underway to further elucidate their occurrences and to quantify them.
3.5. Quantification and Quantitative Variations of Intracellular MC-LR, -RR and -YR
Microcystis aeruginosa cells were identified from all samples collected from December 2010 to March 2011. Freeze-dried algal samples were treated similarly during MC extraction. To minimise instrumental and operational errors quantifications were performed in triplicate to generate mean values for each MC congener (Table 2). Complete removal of pigments and/or organic matter was achieved through liquid-partitioning procedures using CHCl3 as a non-polar solvent mixed with aqueous methanol prior to SPE . When not properly removed from algal samples, green pigments and organic matter lead to SPE cartridge blockages, prolonged extraction time, and poor LC-MS spectra resulting in problematic quantification  and low yields of MCs due to pigment influenced degradation of MCs  and signal interferences . Higher recoveries of MC-RR, -LR and -YR have been demonstrated following a chloroform-methanol partitioning step prior to SPE protocol  resulting in clean and quantifiable LC-MS spectra. The insolubility of MCs in chloroform is therefore of particular advantage in the isolation and LC-MS quantification of MCs following a partitioning step using chloroform-methanol solvent system prior to SPE protocol. In this study clean LC-MS spectra were obtained following a liquid-partitioning-SPE procedure (data not shown). Microcystin-RR, -LR and -YR were quantified using peak areas substituted on linear regression equations: Y = 5,342x − 4,218: (R2 = 0.9963), Y = 4,030x − 2,518: (R2 = 0.9946), and Y = 3,098x + 1,172: (R2 = 0.9948) of standard curves for MC-RR, -LR and -YR solutions (0.5, 1.0, 2.0, 4.0, 6.0, 8.0 and 10.0 µg/mL), respectively. Monthly mean concentrations (n = 3) were calculated for each MC congener and total MC concentrations were shown (Table 2). Aquatic environments are dynamically non-uniform in nature leading to the existence of micro-environments within any given water system. The existence of micro-environments has been shown to influence and govern factors involved in the development of algal blooms and distributions, MC productions and quantitative variations, both in time and space . Micro-environmental dynamics regulate important growth factors, particularly N/P nutrient ratios, thereby affecting growth rates of MC-producing algal blooms leading to variations in MC content [90,91]. From information given in Table 1 and Figure 2 it was shown that there were visible variations in the amounts of intracellular MCs among sites as well as on a monthly basis indicating that MC production was governed by differences in micro-environments within the dam . Basically, MC-RR accounted for the highest amounts of all MCs quantified at all sites and over the four months of the sampling period (Table 1, Figure 2), however, statistically, a one-way ANOVA showed that there was no significant difference in MC concentrations among months, and however, marginal significant difference among MC congeners was observed (P = 0.62 and P = 0.06, respectively) (Figure 3A and C). On the other hand, a one-way ANOVA showed that there was a significant difference (P < 0.001) in MC concentrations among sites. The highest total MC concentration of about 468 µg/g DW was recorded at Site S2 in February 2011 (Table 2). These results support the information about historical massive concentrations of algae  around this area, particularly M. aeruginosa cells. A multivariate analysis to determine effects of interactions between sites and MC congener on MC concentration was performed using ANCOVA (Table 3). Results showed that there was a highly significant influence of the sampling sites (P < 0.001) resulting in quantitative inter-site (spatial) MC variations (Table 2 and Table 3). However, we did not find any significant interaction between period of sampling and site (P = 0.5764), a probable indication that the same species producing MCs was dominant throughout study. Microcystin content variations, including short-term (temporal), inter-site (spatial), perennial as well as seasonal variations, are a common trend in many eutrophic systems due to changing environmental factors and species succession/or dynamics . Publications on intracellular and/or extracellular MC content variations, including temporal/short-term/or inter-site (spatial) variations, have appeared in which either laboratory or actual environmental samples were investigated, including the most recent findings published [44,76,92,93,94,95], etc. Detailed referenced work on this subject was shown in Kardinaal et al.  and Briand et al. . Thus, the observed inter-site variations in intracellular MC concentrations in the Hartbeespoort Dam were not uncommon considering the size of the dam. Moreover, this study was arguably done during the summer season immediately before the onset of the colder season when M. aeruginosa undergoes overwintering [96,97], thus it is our assumption that we were able to capture typical trends in intracellular MC profiles from samples collected representing the dam situation during the summer season. Temporal distribution of Microcystis spp. responsible for MC production in the Hartbeespoort Dam has been demonstrated in the paper published by Van Ginkel et al. , however, quantitative evaluations of MC dominances were not shown. In her report Van Ginkel  reported that cyanobacterial cells increased in a pool with time from the beginning of the summer season and decreased at the onset of the colder season from March towards the winter months, a probable indication that Microcystis cells were overwintering. From the observations made during our study, the MC profiles are evenly distributed across the dam as they were shown to occur in all samples studied, implying that they are produced from one dominant and well-distributed species, M. aeruginosa. Our findings therefore corroborate those of previous studies which showed that M. aeruginosa is a dominant MC-producing species in the Hartbeespoort Dam [25,38,46,48,50,86,98].
|Month||Site||Temp(°C)||Surface water temperature (avg. °C)||Conductivity (µS/cm)||Dissolved oxygen (mg/L)||pH|
|S1||24.6||578.9 ± 0.77||8.6 ± 0.35||8.4 ± 0.07|
|December||S2||25.2||24.8||586.3 ± 0.92||8.4 ± 0.28||8.2 ± 0.07|
|2010||S3||24.8||568.3 ± 1.55||7.7 ± 0.21||8.7 ± 0.07|
|S4||24.7||561.9 ± 0.56||7.3 ± 0.21||8.5 ± 0.14|
|S1||26.2||562.6 ± 2.47||7.3 ± 0.28||8.2± 0.07|
|January||S2||25.8||25.9||559.7 ± 1.13||7.8 ± 0.21||7.9 ± 0.07|
|2011||S3||25.4||558.9 ± 0.98||7.0 ± 0.14||8.4 ± 0.14|
|S4||26.2||578.3 ± 1.2||7.3 ± 0.21||8.0 ± 0.07|
|S1||25.2||555.3 ± 2.05||6.0 ± 0.35||7.8 ± 0.14|
|February||S2||25.7||25.3||549.3 ± 0.64||3.4 ± 0.35||7.4 ± 0.07|
|2011||S3||25.1||561.9 ± 1.69||3.8 ± 0.14||8.5 ± 0.14|
|S4||25.3||554.9 ± 2.62||5.1 ± 0.28||8.3 ± 0.21|
|S1||24.7||564.3 ± 0.64||6.2 ± 0.21||8.1 ± 0.14|
|March||S2||24.2||24.5||559.2 ± 1.48||3.3 ± 0.21||8.2 ± 0.14|
|2011||S3||24.9||560.5 ± 0.98||3.2 ± 0.14||8.7 ± 0.07|
|S4||24.4||559.7 ± 1.13||3.5 ± 0.14||8.8 ± 0.21|
|MC-Congener||Site S1||Site S2|
|MC-RR||21.96 ± 0.16||45.7 ± 2.9||50.46 ± 2.66||49.56 ± 1.62||88.56 ± 1.84||213.78 ± 17.76||268.16 ± 8.06||197.2 ± 2.87|
|MC-YR||7.24 ± 0.48||8.02 ± 0.4||14.12 ± 0.13||9.74 ± 0.58||15.78 ± 0.72||47.2 ± 1.58||71.22 ± 2.74||69.12 ± 1.4|
|MC-LR||6.46 ± 0.86||4.16 ± 0.54||17.26 ± 0.28||13.48 ± 0.52||57.58 ± 3.86||140.68 ± 2.88||128.66 ± 3.36||124.78 ± 3.02|
|TOTAL MC (µg/g DW)||35.66 ± 1.5||57.88 ± 3.84||81.84 ± 3.07||72.78 ± 2.72||161.92 ± 6.42||401.68 ± 22.42||468.04 ± 13.16||391.1 ± 7.29|
|MC-Congener||Site S3||Site S4|
|MC-RR||5.94 ± 0.16||10.68 ± 0.34||16.78 ± 1.1||15.9 ± 0.94||13.78 ± 0.38||17.12 ± 0.2||15.98 ± 0.56||14.04 ± 0.64|
|MC-YR||0.22 ± 0.002||0.68 ± 0.04||3.34 ± 0.22||2.97 ± 0.28||0.14 ± 0.02||1.54 ± 0.02||1.72 ± 0.04||1.34 ± 0.06|
|MC-LR||5.24 ± 0.1||11.34 ± 0.18||9.12± 0.08||6.002 ± 0.2||3.78 ± 0.18||6.32 ± 0.08||5.82 ± 0.46||0.38 ± 0.04|
|TOTAL MC (µg/g DW)||11.4 ± 0.26||22.7 ± 0.56||29.24 ± 1.4||24.87 ± 1.42||17.7 ± 0.58||24.98 ± 0.015||23.52 ± 1.06||15.76 ± 0.74|
|% MC-RR||52.10||47.05 *||57.38||63.93||77.85||68.53||67.94||89.08|
|% MC-LR||45.96||49.95 *||31.19||24.13||21.56||25.3||24.74||2.41|
* Observed anomaly: MC-LR > MC-RR > MC-YR.
|Entity||DF||Sum||Sq mean||Sq F value||Pr (>F)|
* Significant difference at P < 0.05.
3.6. Health Implications of MC-RR Dominance and the Occurrence of (D-Asp3, Dha7)MC-RR Congener
From this study, the observed MC-RR concentrations in the dam were found to be between 5.94 µg/g and 268 µg/g DW (Table 2) among sites. This range of concentration is within and above the range detrimental to detoxifying organs found in fish, as described in the literature . Based on mouse assay the toxicity level of MC-RR (LD50 = 200 µg/g to 800 µg/kg bw) is less than that of MC-LR (LD50 = 25 µg/g to 50 µg/kg bw) , however, Ito et al.  showed that both MC-RR and MC-LR equally inhibit the activities of PP1 and 2A enzymes. The inhibition of PP1 and PP2A activities results in metabolic dysfunction in animals and eventual death in case of higher dosages . In addition, it has also been demonstrated that at elevated concentrations, MC-RR congener had inhibitory effects against antioxidant and detoxification activities of GST on fish gills [99,102] at a dose reaching 10 µg/L. MC-RR is the dominant congener in the Hartbeespoort Dam, toxicologically, however, the fact that its dominance would therefore pose the major health hazard may be ignored, since it is the uptake rate [90,103], synergistic effects of other compounds/or MCs [37,103] and the amount  of MCs ingested that are physiologically more important in terms of animal poisoning than toxicity values of any particular pure MC congener. For instance, bioaccumulation of MC-RR in fish and plant tissues resulting from its elevated extracellular concentration in water  is of importance, as toxicological effects pose health risks for the public consuming seafood products from this water as well as other uses of the water for domestic, recreational and agricultural activities. Although there is no guideline for MC-RR concentrations in recreational waters due to its low toxicity , the WHO has set a limit of 25 µg MC-LR eq/L for total MC concentration in recreational waters . Therefore, from Table 2, it can be deduced that upon cell lysis in Hartbeespoort Dam by the end of the summer season, MC-RR would have contributed the highest proportion to the total MC concentration in recreational water, above the WHO threshold level for recreational waters. However, as described above, upon ingestion or dermatological contact, both MC-RR and MC-LR equally inhibit the activities of PP1 and 2A enzymes, thus elevated concentrations of MC-RR alone could potentially pose a health risk to the general consumers of products or services from the dam.
In addition, Blom and co-workers , showed that the toxicity activity of [D-Asp3, (E)-Dha7]MC-RR was higher than that of the MC-RR congener to algae grazers. Thus, although further investigation is still needed to fully characterise the structure of (D-Asp3, Dha7)MC-RR isolated from the algal extracts we studied, its occurrence in Hartbeespoort Dam is of particular interest to us with regard to what could be its synergistic effect (if any) on the toxicity of the dominant congener, MC-RR and the like.
The quantitative profiles, spatial distribution and the dominance of the MC-RR congener over MC-LR and MC-YR in Hartbeespoort Dam across all sites as well as the occurrence of MC-WR, MC-(H4)YR and (D-Asp3, Dha7)MC-RR in the summer season were reported and related to M. aeruginosa dominance. The information presented here about the identification of sites with higher MC concentrations, MC distribution and dominance in the dam is of particular importance to the Hartbeespoort Dam authorities, researchers and the general public for risk assessments and water safety purposes. The formulation of strategic interventions to minimise potential health risks to the public using such water is highly dependent on information of this kind, especially wherever high-risk sites are identified . Thus, it is the authors’ view that information contained in this document has highlighted existing knowledge and has integrated the new knowledge with the existing knowledge to gain new insights into the state of safety of Hartbeespoort Dam water resources with respect to domestic, agricultural and recreational activities around and downstream of the dam.
Authors are grateful to the WB-STHE project (Dar es Salaam, Tanzania) and the University of Johannesburg (RSA) for their financial support. We also would like to thank the two anonymous reviewers whose generous views and comments on the draft manuscript helped us shape this final document. And finally thanks are due to Ingrid Buchan for proof reading the manuscript.
- Carmichael, W.W. Cyanobacteria secondary metabolites—The cyanotoxins. J. Appl. Bacteriol. 1992, 72, 445–459. [Google Scholar] [CrossRef]
- Sivonen, K.; Jones, G. Cyanobacterial Toxins. Reference. In Toxic Cyanobacteria in Water: A Guide to Their Public Health Consequences; Monitoring and Management; Chorus, I., Bartram, J., Eds.; E&FN Spon: London, UK, 1999; pp. 55–124, Chapter 3. [Google Scholar]
- WHO, Toxic Cyanobacteria in Water: A Guide to their Public Health Consequences; Monitoring and Management; Chorus, I., Bartram, J., Eds.; E&FN Spon: London, UK, 1999; pp. 1–400.
- Anderson, D.M.; Glibert, P.M.; Burkholder, J.M. Harmful algal blooms and eutrophication nutrient sources: Composition and consequences. Estuaries 2002, 25, 704–726. [Google Scholar] [CrossRef]
- Watanabe, M.F.; Oishi, S.; Matsuura, K.; Kawai, H.; Suzuki, M. Toxins contained in Microcystis species of cyanobacteria (blue-green algae). Toxicon 1988, 26, 1017–1025. [Google Scholar] [CrossRef]
- Rinehart, K.L.; Harada, K.; Namikoshi, M.; Chen, C.; Harvis, C.A.; Munro, M.H.G.; Blunt, J.W.; Mulligan, P.; Beasley, E.V.R.; Dahlem, A.M.; Carmichael, W.W. Nodularin, microcystin and the configuration of Adda. J. Am. Chem. Soc. 1988, 110, 8557–8558. [Google Scholar]
- Maizels, M.; Budde, W.A. LC/MS method for the determination of cyanobacteria toxins in water. Anal. Chem. 2004, 76, 1342–1351. [Google Scholar] [CrossRef]
- Sivonen, K.; Namikoshi, M.; Evans, W.R.; Carmichael, W.W.; Sun, F.; Ruhiainen, L.; Luukkainen, R.; Rinehart, K.L. Isolation and characterization of a variety of microcystins from seven strains of cyanobacterial genus Anabaena. Appl. Environ. Microbiol. 1992, 58, 2495–2500. [Google Scholar]
- Rinehart, K.L.; Namikoshi, M.; Choi, B.W. Structure and biosynthesis of toxins from blue-green algae (cyanobacteria). J. Appl. Phycol. 1994, 6, 159–176. [Google Scholar] [CrossRef]
- Metcalf, J.S.; Bell, S.G.; Codd, G.A. Colorimetric immuno-protein phosphatase inhibition assay for specific detection of microcystins and nodularins of cyanobacteria. Appl. Environ. Microbiol. 2001, 67, 904–909. [Google Scholar] [CrossRef]
- Choi, W.B.; Noh, H.Y.; Lee, J.-S. Studies on the structure and biological activity of microcystins produced from Korean cyanobacteria; Microcystis species. J. Korean Ind. Eng. Chem. 1997, 8, 610–616. [Google Scholar]
- Hoeger, S.J.; Schmid, D.; Blom, J.F.; Ernst, B.; Dietrich, D.R. Analytical and Functional Characterization of Microcystins [Asp3]MC-RR and [Asp3, Dhb7]MC-RR: Consequences for Risk Assessment? Environ. Sc. Technol. 2007, 41, 2609–2616. [Google Scholar] [CrossRef]
- Msagati, T.A.M.; Siame, B.A.; Shushu, D.D. Evaluation of methods for isolation, detection and quantification of cyanobacterial hepatotoxins. Aquat. Toxicol. 2006, 78, 282–297. [Google Scholar]
- Fischer, W.J.; Gartwaite, I.; Mile, C.O.; Ross, K.M.; Aggen, J.B.; Chamberlin, A.R.; Towers, N.R.; Dietrich, D.D. Congener-independent immunoassay for microcystins and nodularins. Environ Sci. Technol. 2001, 35, 4849–4856. [Google Scholar] [CrossRef]
- Meriluoto, J.A.O.; Eriksson, J.E.; Harada, K.; Dahlem, A.M.; Sivonen, K.; Carmichael, W. Internal surface reversed-phase high performance liquid-chromatographic separation of the cyanobacterial peptide toxins microcystin-LA; -LR; -YA; -RR and nodularin. J. Chromatogr. 1990, 509, 390–395. [Google Scholar] [CrossRef]
- Lawton, L.A.; Edwards, C.; Codd, G.A. Extraction and high-perfomance liquid chromatography method for the determination of microcystins in raw and treated waters. Analyst 1994, 119, 1525–1530. [Google Scholar] [CrossRef]
- Ward, C.J.; Beattie, K.A.; Lee, E.Y.C.; Codd, G.A. Colorimetric protein phosphatase inhibition assay of laboratory strains and natural blooms of cyanobacteria: Comparisons with high-performance liquid chromatographic analysis for microcystins. FEMS Microbiol. Lett. 1997, 153, 465–473. [Google Scholar] [CrossRef]
- Nicholson, B.C.; Burch, M.D. Evaluation of Analytical Methods for Detection and Quantification of Cyanotoxins in Relation to Australian Drinking Water Guidelines. Available online: http://www.nhmrc.gov.au/_files_nhmrc/publications/attachments/eh22.pdf?q=publications/synopses/_files/eh22.pdf (accessed on 14 May 2012).
- Hummert, C.; Dahlmann, J.; Reinhardt, K.; Dang, H.P.H.; Luckas, B. Liquid chromatography-mass spectrometry identification of microcystins in Microcystis aeruginosa strain from Lake Thanh Cong, Hanoi, Vietnam. Chromatography 2001, 54, 569–575. [Google Scholar] [CrossRef]
- Lawrence, J.F.; Menard, C. Determination of microcystins in blue-green algae, fish and water using liquid chromatography with ultraviolet detection after sample clean-up employing immunoaffinity chromatography. J. Chromatogr. A 2001, 922, 111–117. [Google Scholar] [CrossRef]
- Trojanowicz, M. Chromatographic and capillary electrophoretic determination of microcystins. J. Sep. Sci. 2010, 33, 337–359. [Google Scholar] [CrossRef]
- Harding, W.R.A. Research Strategy for the Detection and Management of Algal Toxins in Water Sources. In WRC Report No. TT 277/06; Development of a Research Strategy for the Detection and Management of Algal Toxins in Water Sources in South Africa (WRC Consultancy K8/576); Water Research Commission: Pretoria; South Africa, 2006; pp. 1–60. [Google Scholar]
- Song, L.; Chen, W.; Peng, L.; Wan, N.; Gan, N.; Zhang, X. Distribution and bioaccumulation of microcystins in water columns: A systematic investigation into the environmental fate and the risks associated with microcystins in Meiliang Bay; Lake Taihu. Water Res. 2007, 41, 2853–2864. [Google Scholar] [CrossRef]
- Van Ginkel, C.E. A National Survey of the Incidence of Cyanobacterial Blooms and Toxin Production in Major Impoundments. In Internal Report No. N/0000/00/DEQ/0503. Resource Quality Services; Department of Water Affairs and Forestry: Pretoria, South Africa, 2004. [Google Scholar]
- Oberholster, P.J.; Botha, A.-M. Use of remote sensing and molecular markers to detect toxic cyanobacterialhyperscum crust: A case study on Lake Hartbeespoort; South Africa. Afr. J. Biotechnol. 2010, 9, 8791–8799. [Google Scholar]
- Jayatissa, L.P.; Silva, E.I.L.; McElhineynd, J.; Lawton, L.A. Occurrence of toxigeniccyanobacterial blooms in freshwaters of Sri Lanka. System. Appl. Microbiol. 2006, 29, 156–164. [Google Scholar] [CrossRef]
- Von Sperling, E.; Ferreira, A.C.S.; Gomes, L.N.L. Comparative eutrophication development in two Brazilian water supply reservoirs with respect to nutrient concentrations and bacteria growth. Desalination 2008, 226, 169–174. [Google Scholar] [CrossRef]
- Sivonen, K. Effects of light, temperature, nitrate, orthophosphate, and bacteria on growth of and hepatotoxin production by Oscillatoria agardhii strains. Appl. Environ. Microbiol. 1990, 56, 2658–2666. [Google Scholar]
- Rapala, J.; Sivonen, K.; Lyra, C.; Niemela, S.I. Variation of microcystins, cyanobacterial hepatotoxins, in Anabaena spp. as a function of growth stimuli. Appl. Environ. Microbiol. 1997, 63, 2206–2212. [Google Scholar]
- Tsuji, K.; Watanuki, T.; Kondo, F.; Watanabe, M.F.; Nakazawa, H.; Sujuki, M.; Uchida, H.; Harada, K.I. Stability of microcystins from cyanobacteria-IV. Effect of chlorination on decomposition. Toxicon. 1997, 35, 1033–1041. [Google Scholar] [CrossRef]
- Butler, N.; Carlisle, J.C.; Linville, R.; Washburn, B. Microcystins: A Brief Overview of Their Toxicity and Effects, with Special Reference to Fish, Wildlife, and Livestock; Ecotoxicology Program Integrated Risk Assessment Branch Office of Environmental Health Hazard Assessment California Environmental Protection Agency: Sacramento, CA, USA, 2009; pp. 1–17. [Google Scholar]
- Azevedo, S.M.F.O.; Carmichael, W.W.; Jochimsen, E.M.; Rinehart, K.L.; Lau, S.; Shaw, G.R.; Eaglesham, G.K. Human intoxication by microcystins during renal dialysis treatment in Caruaru-Brazil. Toxicol. 2002, 181-182, 441–446. [Google Scholar] [CrossRef]
- Mur, L.R.; Skulberg, O.M.; Utkilen, H. Cyanobacteria in the Environment. In Toxic Cyanobacteria in Water: A Guide to Their Public Health Consequences; Monitoring and Management; Chorus, I., Bartram, J., Eds.; E&FN Spon: London, UK, 1999; pp. 25–54. [Google Scholar]
- Arto, A.; Lehtimaki, J.; Mattilai, K.; Eriksson, J.E.; Sivonen, K.; Tapio, T.R.; Drakenberg, T. Solution structure of nodularin. An inhibitor of serine/threonine-specific protein phosphatases. J. Biol. Chem. 1996, 271, 16695–16702. [Google Scholar]
- Metcalf, J.S.; Codd, G.A. Microwave oven and boiling waterbath extraction of hepatotoxins from cyanobacterial cells. FEMS Microbiol. Lett. 2000, 184, 241–246. [Google Scholar] [CrossRef]
- Park, H.D.; Watanabe, M.F.; Harada, K.I.; Suzuki, M.; Hayashi, H.; Okino, T. Seasonal variations of Microcystis species and toxic heptapeptidemicrocystins in Lake Suwa. Environ. Toxicol. Water Qual. 1993, 8, 425–435. [Google Scholar] [CrossRef]
- Fitzgeorge, R.B.; Clatk, S.A.; Keevil, C.W. Reference. In Detection Methods for Cyanobacterial Toxins; Codd, G.A., Jefferies, T.M., Keevil, C.W., Potter, E., Eds.; The Royal Society of Chemistry: London, UK, 1994; pp. 69–74. [Google Scholar]
- Harding, W.R.; Paxton, B.R. Cyanobacteria in South Africa. A Review. In WRC Report No. TT 153/01; Water Research Commission: Pretoria, South Africa, 2001. [Google Scholar]
- Ibelings, B.W.; Chorus, I. Accumulation of cyanobacterial toxins in freshwater “seafood” and its consequences for public health: A review. Environ. Pollut. 2007, 150, 177–192. [Google Scholar]
- Papadimitriou, T.; Kagalou, I.; Stalikas, C.; Pilidis, G.; Leonardos, I.D. Assessment of microcystin distribution and biomagnifications in tissues of aquatic food web compartments from a shallow lake and evaluation of potential risks to public health. Ecotoxicol. 2012, 2, 1155–1166. [Google Scholar]
- Pflugmacher, S.; Wiegand, C.; Beattie, K.A.; Codd, G.A.; Steinberg, C.E.W. Uptake of the cyanobacterialhepatotoxinmicrocystin-LR by aquatic macrophytes. J. Appl. Bot. 1998, 72, 228–232. [Google Scholar]
- Lance, E.; Brient, L.; Bormans, M.; G’erard, C. Interactions between cyanobacteria and gastropods I. Ingestion of toxic Planktothrix agardhii by Lymnaea stagnalis and the kinetics of microcystin bioaccumulation and detoxification. Aquat. Toxicol. 2006, 79, 140–148. [Google Scholar] [CrossRef]
- Prakash, S.; Lawton, L.A.; Edwards, C. Stability of toxigenic Microcystis blooms. Harmful Algae. 2009, 8, 377–384. [Google Scholar] [CrossRef]
- Dai, R.; Liu, H.; Qu, J.; Ru, J.; Hou, Y. Cyanobacteria and their toxins in Guanting reservoir of Beijing, China. J. Haz. Mat. 2007, 153, 470–477. [Google Scholar]
- Oberholster, J.P.; Myburg, G.J.; Govender, D.; Bengis, R.; Botha, A.-M. Identification of toxigenic Microcystis strains after incidents of wild animal mortalities in the Kruger National Park, South Africa. Ecotoxicol. Environ. Saf. 2009, 72, 1177–1182. [Google Scholar] [CrossRef]
- Wicks, R.J.; Thiel, P.G. Environmental factors affecting the production of peptide toxins in floating scums of the cyanobacterium Microcystis aeruginosa in a hypertrophic African reservoir. Environ. Sci. Technol. 1990, 24, 1413–1418. [Google Scholar] [CrossRef]
- Van Ginkel, C.E.; Silberbauer, M.J.; Vermaak, E. The seasonal and spatial distribution of cyanobacteria in South African surface waters. Verh. Internat. Verein. Limnol. 2000, 27, 871–878. [Google Scholar]
- Downing, T.G.; Van Ginkel, C.E. Cyanobacterial Monitoring 1990–2000: Evaluation of SA data. In WRC Report No. 1288/1/04; Water Research Commission: Pretoria, South Africa, 2004; pp. 1–44. [Google Scholar]
- Park, H.-D.; Iwami, C.; Watanabe, M.F.; Harada, K.-I.; Okino, T.; Hayashi, H. Temporal variabilities of the concentrations of intra- and extracellular microcystin and toxic Microcystis species in a hypertrophic lake, Lake Suwa, Japan (1991–1994). Environ. Toxicol. Water Qual. 1998, 13, 61–72. [Google Scholar] [CrossRef]
- Msango, M.G. A Comparative Analysis of the Cytotoxicity of Cyanotoxins using In-Vitro (Cell Culture) and In-Vivo (Mouse) Assays. MS Thesis, University of Pretoria, Pretoria, South Africa, 2007..
- Conti, R.A.L.; Guerrero, J.M.; Regueira, J.M. Levels of microcystins in two Argentinean reservoirs used for water supply and recreation: Differences in the implementation of safe levels. Environ. Toxicol. 2005, 20, 263–269. [Google Scholar] [CrossRef]
- Moreno, M.I.; Herrador, A.; Atencio, L.; Puerto, M.; Gonzalez, G.; Camean, M.A. Differentiation between microcystin contaminated and uncontaminated fish by determination of un-conjugated MCs using an ELISA anti-Adda test based on receiver-operating characteristic curves threshold values: Application to Tinca tinca from natural ponds. Environ. Toxicol. 2009, 26, 45–56. [Google Scholar]
- An, J.; Carmichael, W.W. Use of a colorimetric protein phosphatase inhibition assay and enzyme linked immunosorbent assay for the study of microcystins and nodularins. Toxicon 1994, 32, 1495–1507. [Google Scholar] [CrossRef]
- Fischer, W.J.; Garthwaite, I.; Miles, C.O.; Ross, K.M.; Aggen, J.B.; Chamberlin, A.R.; Towers, N.R.; Dietrich, D.R. Congener-independent immunoassay for microcystins and nodularins. Environ. Sci. 2001, 35, 4849–4856. [Google Scholar] [CrossRef]
- Metcalf, J.S.; Beattie, K.A.; Ressler, J.; Gerbersdorf, S.; Pﬂugmacher, S.; Codd, G.A. Cross-reactivity and performance assessment of four microcystin immunoassays with detoxication products of the cyanobacterial toxin, microcystin-LR. J. Water Res. Tech-Aqua. 2002, 51, 145–151. [Google Scholar]
- Hoeger, S.J.; Hitzfeld, B.C.; Dietrich, D.R. Occurrence and elimination of cyanobacterial toxins in drinking water treatment plants. Toxicol. Appl. Pharmacol. 2005, 203, 231–242. [Google Scholar] [CrossRef]
- Hoeger, S.J.; Shaw, G.; Hitzfeld, B.C.; Dietrich, D.R. Occurrence and elimination of cyanobacterial toxins in two Australian drinking water treatment plants. Toxicon 2004, 43, 639–649. [Google Scholar] [CrossRef]
- Cardozo, K.H.M.; Carvalho, V.M.; Pinto, E.; Colepicolo, P. Fragmentation of mycosporine-like amino acids by hydrogen/deuterium exchange and electrosprayionisation tandem mass spectrometry. Rapid Commun. Mass Spectrom. 2006, 20, 253–258. [Google Scholar]
- Cameán, A.; Moreno, I.M.; Ruiz, M.J.; Pico, Y. Determination of microcystins in natural blooms and cyanobacterial strain cultures by matrix solid-phase dispersion and liquid chromatography-mass spectrometry. Anal. Bioanal. Chem. 2004, 380, 537–544. [Google Scholar] [CrossRef]
- Kondo, F.; Ikai, Y.; Oka, H.; Ishikawa, N.; Watanabe, M.F.; Watanabe, M.; Harada, K.-I.; Suzuki, M. Separation and identification of microcystins in cyanobacteria by frit-fast atom bombardment liquid chromatography-mass spectrometry. Toxicon 1992, 30, 227–237. [Google Scholar] [CrossRef]
- Bateman, K.P.; Thibault, P.; Douglas, D.J.; White, R.L. Mass spectral analyses of microcystins from toxic cyanobacteria using on-line chromatographic and electrophoretic separations. J. Chromatogr. A 1995, 712, 253–268. [Google Scholar] [CrossRef]
- Messineo, V.; Bogialli, S.; Melchiorre, S.; Sechi, N.; Luglie, A.; Cassidu, P.; Marian, A.M. Cyanobacterial toxins in Italian freshwaters. Limnol. 2009, 39, 95–106. [Google Scholar] [CrossRef]
- R Development Core Team, Reference. In R: A Language and Environment for Statistical Computing; R Foundation for Statistical Computing: Vienna, Austria, 2011.
- Department of Water Affairs, Hartbeespoort Government Water Scheme; Department of Water Affairs: Pretoria, South Africa, 1991; pp. 1–6.
- Harding, W.R.; Downing, T.G.; Van Ginkel, C.E.; Moolman, A.P.M. An overview of cyanobacterial research and management in South Africa post-2000. Water SA 2009, 35, 479–484. [Google Scholar]
- Harding, W.R.; Thornton, J.A.; Steyn, G.; Panuska, J.; Morrison, I.R. Hartbeespoort Dam Remediation Project (Phase I). Action Plan (Volume I) Final Report; Department of Agriculture, Conservation, Environment and Tourism Project 58/2003; Department of Agriculture, Conservation, Environment and Tourism of the North West Province Government (DACET, NWP): Mmabatho, South Africa, 2004; pp. 1–158. [Google Scholar]
- Steyn, D.J.; Toerien, D.F. Eutrophication levels of some South African impoundments. II. Hartbeespoort Dam. Water SA 1975, 1, 93–101. [Google Scholar]
- . Department of Water Affairs and Forestry, HartbeespoortDam Integrated Biological Remediation Programme; Department of Water Affairs and Forestry: Pretoria, South Africa, 2007; pp. 1–18.
- Falconer, I.R.; Humpage, A.R. Health risk assessment of cyanobacterial (blue-green algal) toxins in drinking water. Int. J. Environ. Res. Public Health 2005, 2, 43–50. [Google Scholar] [CrossRef]
- Hötzel, G.; Croome, R. A Phytoplankton Methods Manual for Australian Freshwaters; LWRRDC Occasional Paper 22/99; Land and Water Resources Research and Development Cooperation: Canberra, Australia, 1999; pp. 1–58. [Google Scholar]
- Owuor, K.; Okonkwo, J.; Van Ginkel, C.; Scott, W. Environmental Factors Affecting the Persistence of Toxic Phytoplankton in the Hartbeespoort Dam; WRC Report No. 1401/3/07; Water Research Commission: Pretoria, South Africa, 2007. [Google Scholar]
- Haarhoff, J.; Langenegger, O.; Van der Merwe, P.J. Practical aspects of water treatment plant design for a hypertrophic impoundment. Water SA 1992, 18, 27–36. [Google Scholar]
- Jacoby, J.M.; Collier, D.C.; Welch, E.B.; Hardy, J.; Crayton, M. Environmental factors associated with a toxic bloom of Microcystis aeruginosa. Can. J. Fish. Aquat. Sci. 2000, 57, 231–240. [Google Scholar] [CrossRef]
- Jones, S.B.; Jones, J.R. Seasonal variation in cyanobacterial toxin production in two Nepalese lakes. Verh. Internat. Verein. Limnol. 2002, 28, 1017–1022. [Google Scholar]
- Dziallas, C.; Grossart, H.-P. Microbial interactions with the cyanobacterium Microcystis aeruginosa and their dependence on temperature. Mar. Biol. 2012. [Google Scholar]
- Lee, S.J.; Jang, M.-H.; Kim, H.-S.; Yoon, B.-D.; Oh, H.-M. Variation of microcystin content of Microcystis aeruginosa relative to the N:P ratio and growth stage. J. Appl. Microbiol. 2000, 89, 323–329. [Google Scholar] [CrossRef]
- Greenwald, I. The Solubility of Calcium Phosphate I. The Effect of pH and of Amount of Solid Phase. Available online: http://www.jbc.org/content/143/3/703.full.pdf (accessed on 10 June 2012).
- Shapiro, J. Blue-green algae in lakes: The role and management significance of pH and CO2. Int. Rev. Gesamten. Hydrobiol. 1990, 69, 765–780. [Google Scholar] [CrossRef]
- Kardinaal, W.E.A.; Visser, P.M. Dynamics of cyanobacterial toxins: Sources of variability in microcystin concentrations. In Harmful Cyanobacteria; Huisman, J., Matthijs, H.C.P., Visser, P.M., Eds.; Springer-Verlag: Berlin, Germany, 2005; pp. 41–63. [Google Scholar]
- Imai, H.; Chang, K.-H.; Kusaba, M.; Nakano, S.-I. Temperature dependent dominance of Microcystis (Cyanophyceae) species: M. aeruginosa and M. wesenbergii. J. Plank. Res. 2009, 31, 171–178. [Google Scholar]
- Amé, M.V.; del Pilar Díaz, M.; Wunderlin, D.A. Occurrence of toxic cyanobacteria bloom in San Roque reservoir (Córdoba, Argentina): A field and chemometric study. Environ. Toxicol. 2003, 18, 192–201. [Google Scholar] [CrossRef]
- Department of Water Affairs. Hartbeespoort Dam Remediation Program—Clear Water State and Algae Concentration. Available online: www.184.108.40.206/hartiesdev/algaesitrep.aspx (accessed on 11 June 2012).
- Namikoshi, M.; Sun, F.; Choi, W.B.; Rinehart, L.K. Seven more microcystins from Homer lake cells: Application of the general method for structure assignment of peptides containing α-β-dehydroamino acid unit(s). J. Org. Chem. 1995, 60, 3671–3679. [Google Scholar] [CrossRef]
- Antoniou, M.G.; Delacruz, A.; Dionysiou, D. Intermediates and reaction pathways from the degradation of microcystin-LR with sulfate radicals. Environ. Sci. Technol. 2010, 44, 7238–7244. [Google Scholar] [CrossRef]
- Spoof, L.; Vesterkvist, P.; Lindholm, T.; Meriluoto, J. Screening for cyanobacterialhepatotoxins, microcystins and nodularin in environmental water samples by reversed-phase liquid chromatography-electrospray ionization mass spectrometry. J. Chromatogr. A 2003, 1020, 105–119. [Google Scholar] [CrossRef]
- Zohary, T. Hyperscum of the cyanobacterium Microcystis aeruginosa in a hypertrophic lake (Hartbeespoort Dam, South Africa). J. Plankton Res. 1985, 7, 399–409. [Google Scholar] [CrossRef]
- Krishnamyrthy, T.; Szafraniec, L.; Hunt, D.F.; Shabanowitz, J.; Yates, J.R.; Hauer, C.R.; Carmichael, W.W.; Skulberg, O.; Codd, G.A.; Missler, S. Structural characterization of toxic cyclic peptides from blue-green algae by tandem mass spectrometry. Proc. Nat. Acad. Soc. USA 1989, 86, 770–774. [Google Scholar] [CrossRef]
- Poon, K.F.; Lam, M.H.W.; Lam, P.K.S.; Wong, B.S.F. Determination of microcystins in cyanobacterial blooms by solid-phase microextraction-high-performance liquid chromatography. Environ. Toxicol. Chem. 2001, 20, 1648–1655. [Google Scholar]
- Phelan, R.R.; Downing, T.G. Optimization of laboratory scale production and purification of microcystin-LR from pure cultures of Microcystis aeruginosa. Afr. J. Biotechnol. 2007, 6, 2451–2457. [Google Scholar]
- Downing, T.G. A Model for Environmental Regulation of Microcystin Production by Microcystis. In WRC Report No. 1401/1/07; Water Research Commission: Pretoria, South Africa, 2007; pp. 1–69. [Google Scholar]
- Briand, E.; Gugger, M.; François, J.-C.; Bernard, C.; Humbert, J.-F; Quiblier, C. Temporal variations in the dynamics of potentially microcystin-producing strains in a bloom-forming Planktothrix agardhii (cyanobacterium) population. Appl. Environ. Microbiol. 2008, 74, 3839–3849. [Google Scholar] [CrossRef]
- Pawlik-Skowrońska, B.; Pirszel, J.; Kornijów, R. Spatial and temporal variations in microcystin concentrations during perennial bloom of Planktothrix agardhii in a hypertrophic lake. Ann. Limnol. Int. J. Lim. 2008, 44, 145–150. [Google Scholar] [CrossRef]
- Indabawa, I.I. Detection of variants of microcystin produced by Microcystis aeruginosa in some burrow pits of Kano, Nigeria. Bajopas. 2009, 2, 189–197. [Google Scholar]
- Sabart, M.; Pobel, D.; Briand, E.; Combourieu, B.; Salençon, M.J.; Humbert, J.F.; Latour, D. Spatiotemporal variations in microcystin concentrations and in the proportions of microcystin-producing cells in several Microcystis aeruginosa populations. Appl. Environ. Microbiol. 2010, 76, 4750–4759. [Google Scholar] [CrossRef]
- Graham, J.L.; Jones, J.R.; Jones, S.B.; Clevenger, T.E. Spatial and temporal dynamics of microcystin in a Missouri Reservoir. Lake Reserve. Manage. 2006, 22, 59–68. [Google Scholar] [CrossRef]
- Latour, D.; Giraudet, H.; Berthon, J.-L. Frequency of dividing cells and viability of Microcystis aeruginosa in sediments of a eutrophic reservoir. Aquat. Microbiol. Ecol. 2004, 36, 117–122. [Google Scholar] [CrossRef]
- Preston, T.; Stewart, W.D.P.; Reynolds, C.S. Bloom-forming Microcystis aeruginosa overwinters on sediment surface. Nature 1980, 288, 365–367. [Google Scholar] [CrossRef]
- Scott, W.E. Occurrence and significance of toxic cyanobacteria in Southern Africa. Water Sci. Technol. 1991, 23, 175–180. [Google Scholar]
- Cazenave, J.; Bistoni, M.A.; Pesce, S.F.; Wunderlin, D.A. Differential detoxification and antioxidant response in diverse organs of Corydora paleatus exposed to microcystin-RR. Aquat. Toxicol. 2006, 76, 1–12. [Google Scholar] [CrossRef]
- Sivonen, K. Cyanobacterial toxins and toxin production. Phycologia 1996, 35, 12–24. [Google Scholar] [CrossRef]
- Ito, E.; Takai, A.; Kondo, F.; Masui, H.; Imanishi, S.; Harada, K. Comparison of protein phosphatase inhibitory activity and apparent toxicity of microcystins and related compounds. Toxicon 2002, 40, 1017–1025. [Google Scholar] [CrossRef]
- Cazenave, J.; Wunderlin, D.A.; Bistoni, M.A.; AME, M.V.; Krause, E.; Pflugmacher, S.; Wiegand, C. Uptake, tissue accumulation and distribution of microcystin-RR in Corydora paleatus, Jenynsia multidentata and Odontesthes bonariensis field and laboratory study. Aquat. Toxicol. 2005, 75, 178–190. [Google Scholar] [CrossRef]
- Osswald, J.; Carvalho, A.P.; Claro, J.; Vasconcelos, V. Effects of cyanobacterial extracts containing anatoxin-a and pure anatoxin-a on early developmental stages of carp. J. Ecotoxicol. Environ. Saf. 2009, 72, 473–478. [Google Scholar] [CrossRef]
- Blom, J.F.; Robinson, J.A.; Jüttner, F. High grazer toxicity of [D-Asp3, (E)-Dha7]MC-RR of Planktothrix rubescens as compared to different microcystins. Toxicon 2001, 39, 1923–1932. [Google Scholar] [CrossRef]
- World Health Organisation (WHO). Guidelines for Safe Recreational Waters. Volume1: Coastal and Fresh Waters; WHO Publishing: Geneva, Switzerland, 2003; p. 136.
© 2012 by the authors; licensee MDPI, Basel, Switzerland. This article is an open-access article distributed under the terms and conditions of the Creative Commons Attribution license (http://creativecommons.org/licenses/by/3.0/).