The effect of power ultrasound on algae blooms (Microcystis aeruginosa) over a 30 minute period was assessed using 200 and 400 mL suspensions of optical density of 2.0 at 680 nm. The frequencies employed were 20, 40, 580 (40%, 80%, and maximum intensity), 864 (40%, 80% and maximum intensity) and 1146 kHz (40%, 80% and maximum intensity). Ultrasound can induce two different effects on algal cells; inactivation at high power (≥ 0.0022 Wcm-3) and de-agglomeration at low power (≤ 0.0042 Wcm-3). Ultrasonic effects were observed using haemocytometer, optical density, UV-visible spectrometer, fluorospectrometer and flow cytometry. Using a 40 kHz bath (0.0214 Wcm-3) led to de-agglomeration resulting in an overall increase in algae of -0.28% by haemocytometer and -4.20% by optical density. The highest inactivation achieved was 91.54% (haemocytometer) and 44.63% (optical density) using 1146 kHz (maximum intensity, 0.0248 Wcm-3) and 200 mL suspension. In terms of efficiency to achieve inactivation (i.e. inactivation % / power) the best result was observed at 864 kHz (40% power setting, 0.0042 Wcm-3) with 200 mL suspension giving 8226.19 by haemocytometer and 5011.90 by optical density. This initial part of the study allowed a comparison to be made of the ultrasonic parameters that would lead to optimum algae removal in terms of acoustic energy input. The haemocytometer results for cells number were generally higher than those indicated by optical density which is probably due to the fact that the former records only cell numbers remaining whereas the latter is an overall measure of algae concentration (ruptured cells will still register, because their contents remain in suspension). Studies on de-agglomeration and inactivation were also undertaken using small or medium-scale ultrasonic equipment that were models for industrial scale systems. The following volumes of algae suspension and equipment were employed: Sonolator (Sonic Corporation, 5L flow), 16 kHz and 20 kHz Dual Frequency Reactor (DFR, Advanced Sonics LLC, 1L static and 3.5 L flow), 20 kHz Vibrating Tray (Advanced Sonics LLC, 1.5L static) and 20 kHz ultrasonic probe (made at Southeast University, 4L static). The most effective inactivation effects were obtained with the DFR reactor in static mode and 60% power setting for 10 minutes which achieved reductions calculated at 79.25% using haemocytometry and 60.44% by optical density. The third part of this study was to gain a greater understanding of the basic mechanisms of the action of ultrasound on algae and to interpret this in terms of its potential for algal cell removal and control. Algal cell activity was assessed by three methods: using a UV-visible spectrometer (Shimazu, 2450PC), a fluorometer (Shimazu, RF5301) and a flow cytometer (BD FACS Calibur). Ultrasonic damage to Chlorophyll A was revealed through observation of the loss in UV-Vis spectrophotometer peaks around 600 nm together with the decrease in fluorometer results for peaks around 500 and 680 nm. Flow cytometer results were able to identify the number of both intact cells and damaged/ruptured cells thus giving greater insight into the mechanism of ultrasonic inactivation. The direct rupture of cells by power ultrasound was prevalent at low frequencies ≤ 40 kHz due to the mechanical effects of cavitation collapse and inactivation of algal cells by free radicals occurred at high frequencies ≥ 100 kHz and medium powers where mechanical effects are much reduced. In conclusion, this work has shown that power ultrasound can provide a suitable method to control algal growth in small and medium laboratory scales. Scale-up beyond this point is the subject of further research but the results herein clearly demonstrate the importance of choosing the correct ultrasonic parameters in terms of frequency, power and exposure time.

Research in the use of ozone in water treatment conducted by many authors support the idea that the nature and characteristics of natural organic matter (NOM) present in raw water determines the efficiency of ozonation in water purification. An ozone contact chamber was designed and made to allow pre-ozonation of water to take place. The concentration of ozone in the chamber was determined using the Indigo method. For the duration of one year, water samples were collected from four different sampling sites and analyzed to determine their overall ecological status with regard to several variables such as pH, chlorophyll-a, SAC254, turbidity, DOC, algal species composition and sum of NOM. Two dams sites and two riverine sites were chosen, Hartbeespoort Dam (a hyper-eutrophic impoundment), Boskop Dam (a mesotrophic impoundment), Midvaal Water Company at Orkney and Sedibeng Water at Bothaville. The samples were treated in Jar Tests with FeCI3 and the same variables were measured. Preozonation followed by Jar Tests was performed on each sample at twoconcentrations of ozone and the variables were measured to examine the efficiency of ozonation. In general, the ph was high and stayed the same for all the samples and for all the treatments. DOC was variable and showed no relationship to any other variable or to the treatments. Hartbeespoort Dam was found to be a eutrophic impoundment characterized by high algal bloom of the cyanobacteria Microcystis sp., Turbidity, SAC254, and the sum of NOM were lower than for the riverine sites but higher than for Boskop Dam. The NOM constituted more intermediate molecular weight(1MW)and low molecular weight (LMW) fractions than the riverine sites. Ozone was effective in reducing chlorophyll-a, turbidity and SAC254 from Hartbeespoort Dam, but the presence of large numbers of algal cells interferes with its efficiency. Release of cell-bound organics after ozonation can lead to increases instead of decreases in these variables. Jar Test results demonstrate that ozonation improves water quality when compared to conventional treatment although the interference of algal cells can alter results. Boskop Dam is a mesotrophic impoundment characterised by low productivity, low SAC254, tow turbidity and low sum of NOM. However, it has a large portion of the LMW fraction of NOM present. This LMW fraction affects the treatment process as this fraction is not acted upon by ozone. Therefore it was found that ozonation did not improve the quality of the water when compared to conventional treatment. The two riverine sites, Midvaal and Sedibeng were similar to each other. Both sites had high algal productivity with high chlorophyll-a values indicative of algal blooms observed at certain times. These blooms consisted either of members of Bacillariophyceae or Chlorophyceae. High turbidity and SAC254 was observed during the rainy season and was related to the high percentage HMW and IMW fractions of NOM present. There was correlation between the turbidity and SAC254 of these sites leading to the assumption that the turbidity of the river is due to the presence of HMW humic fractions of NOM. Ozonation was effective in improving water quality with respect to turbidity, SAC254 and chlorophyll-a removal, both on its own and after conventional treatment when combined with a coagulant. However, the species of algae present affects ozonation as members of Bacillariophyceae are not affected by the actions of ozone because of the presence of a silica frustule whereas members of Chlorophyceae are easily removed by ozone. In general, ozone acts upon the HMW and LMW fractions of NOM causing them to breakdown into smaller fractions. Ozone has no effect on samples that have a high percentage of the LMW fraction of NOM. This LMW fraction is more readily removed by conventional treatment than by ozonation. The presence of large numbers of algal cells as well as the species of cells can negatively affect the treatment process with regard to ozone. / Thesis (M. Environmental Science (Water Science))--North-West University, Potchefstroom Campus, 2007.

Research in the use of ozone in water treatment conducted by many authors support the idea that the nature and characteristics of natural organic matter (NOM) present in raw water determines the efficiency of ozonation in water purification. An ozone contact chamber was designed and made to allow pre-ozonation of water to take place. The concentration of ozone in the chamber was determined using the Indigo method. For the duration of one year, water samples were collected from four different sampling sites and analyzed to determine their overall ecological status with regard to several variables such as pH, chlorophyll-a, SAC254, turbidity, DOC, algal species composition and sum of NOM. Two dams sites and two riverine sites were chosen, Hartbeespoort Dam (a hyper-eutrophic impoundment), Boskop Dam (a mesotrophic impoundment), Midvaal Water Company at Orkney and Sedibeng Water at Bothaville. The samples were treated in Jar Tests with FeCI3 and the same variables were measured. Preozonation followed by Jar Tests was performed on each sample at twoconcentrations of ozone and the variables were measured to examine the efficiency of ozonation. In general, the ph was high and stayed the same for all the samples and for all the treatments. DOC was variable and showed no relationship to any other variable or to the treatments. Hartbeespoort Dam was found to be a eutrophic impoundment characterized by high algal bloom of the cyanobacteria Microcystis sp., Turbidity, SAC254, and the sum of NOM were lower than for the riverine sites but higher than for Boskop Dam. The NOM constituted more intermediate molecular weight(1MW)and low molecular weight (LMW) fractions than the riverine sites. Ozone was effective in reducing chlorophyll-a, turbidity and SAC254 from Hartbeespoort Dam, but the presence of large numbers of algal cells interferes with its efficiency. Release of cell-bound organics after ozonation can lead to increases instead of decreases in these variables. Jar Test results demonstrate that ozonation improves water quality when compared to conventional treatment although the interference of algal cells can alter results. Boskop Dam is a mesotrophic impoundment characterised by low productivity, low SAC254, tow turbidity and low sum of NOM. However, it has a large portion of the LMW fraction of NOM present. This LMW fraction affects the treatment process as this fraction is not acted upon by ozone. Therefore it was found that ozonation did not improve the quality of the water when compared to conventional treatment. The two riverine sites, Midvaal and Sedibeng were similar to each other. Both sites had high algal productivity with high chlorophyll-a values indicative of algal blooms observed at certain times. These blooms consisted either of members of Bacillariophyceae or Chlorophyceae. High turbidity and SAC254 was observed during the rainy season and was related to the high percentage HMW and IMW fractions of NOM present. There was correlation between the turbidity and SAC254 of these sites leading to the assumption that the turbidity of the river is due to the presence of HMW humic fractions of NOM. Ozonation was effective in improving water quality with respect to turbidity, SAC254 and chlorophyll-a removal, both on its own and after conventional treatment when combined with a coagulant. However, the species of algae present affects ozonation as members of Bacillariophyceae are not affected by the actions of ozone because of the presence of a silica frustule whereas members of Chlorophyceae are easily removed by ozone. In general, ozone acts upon the HMW and LMW fractions of NOM causing them to breakdown into smaller fractions. Ozone has no effect on samples that have a high percentage of the LMW fraction of NOM. This LMW fraction is more readily removed by conventional treatment than by ozonation. The presence of large numbers of algal cells as well as the species of cells can negatively affect the treatment process with regard to ozone. / Thesis (M. Environmental Science (Water Science))--North-West University, Potchefstroom Campus, 2007.