Earthworking activities have the potential to accelerate soil erosion through vegetation clearance and soil compaction processes. The eroded sediment can have many detrimental effects on receiving aquatic environments, and thus its discharge is controlled under the Resource Management Act, 1991. Two chemically dosed sediment retentions ponds at the SH20 extension project in Mount Roskill, Auckland were investigated, and the impact of the discharge of one of these ponds on a receiving waterbody was assessed using the Stream Ecological Valuation (SEV) method. Rainfall and suspended solid data was collected for a nine month period between November 2006 and August 2007, although sampling did not commence at one of the ponds until March 2007. Two SEV samples were undertaken within the receiving waterbody; one in November 2006 and the other in November 2007 to assess environmental changes resulting from the sediment retention pond discharge. The suspended solids results measured within the sediment retention ponds during this study were much lower than those reported by other studies on earthwork sites. This is believed to be due to the effective implementation of sediment and erosion control measures onsite. The Somerset Road pond was very effective at removing suspended solids throughout the sampling period, with the majority of suspended solid removal occurring in the forebay as it typically did not become full enough to overflow into the main pond. When the forebay was full of water, the PAC dosing system resulted in large reductions in suspended solid levels over a short horizontal distance within the forebay. A smaller amount of suspended solid reduction was achieved in the main pond, predominately through dilution, with the major function of the main pond being additional storage capacity for runoff. Discharge from the Somerset Road Pond was not continuous due to low water levels in the main pond. However, when discharge did occur, the suspended solids levels were very low compared with other studies investigating sediment retention pond discharge. The Richardson Road pond was less effective at removing suspended solids due to the flow regime within the forebay. There were two runoff channels entering the forebay, as well as a continual flow of groundwater. Only one of the runoff channels was directly dosed with PAC, and as the water level in the forebay was typically at, or just below, the level spreader at all times, there was a decreased potential for the PAC to become evenly distributed through the forebay and achieve dosing of all runoff. Furthermore, the main pond discharged continuously during the study period, resulting in reduced residence times of runoff within the pond system. Nonetheless, the discharge from the main pond was much lower than other studies, implying suspended solid reduction was being achieved. The SEV method indicated that the receiving environment was already degraded due to modifications to the riparian vegetation, increased dissolved oxygen demand, and moderate bank erosion. This was reflected in the macroinvertebrate population, with only pollution tolerant taxa being collected, thus limiting the use of macroinvertebrates as an assessment tool in this study. However, the SEV method, which assesses a wide range of ecological functions, implied that very little environmental change occurred as a result of the sediment retention pond discharge. A small increase in deposited sediment was observed on the stream bed, however indications are that deposited sediment is rapidly washed away once earthworks are completed. Thus this deposited sediment may not have a permanent impact within the receiving environment.

The success of surface water treatment strongly depends on the effectiveness of coagulant performance. Aluminium sulfate (alum), the most widely used coagulant in water treatment plants in Canada, is well known for its poor performance in cold water. Polyaluminium chloride (PACl), a relatively new polymeric aluminium coagulant increasingly being used in water treatment plants, is found to have many advantages over conventional alum. However, PACl hydrolysis reaction is quite complex and its action is not fully understood. In this research, a series of bench-scale jar tests with alum and PACl was conducted. Alum and PACl coagulation flocs were analyzed for the evaluation of coagulant performances at 19C and 5C for the Split Lake water treatment plant. The results of this research indicated that the settling properties of PACl flocs were superior to those of alum flocs, especially at the lower temperature. The average size of PACl flocs was relatively smaller than that of alum flocs. The density of PACl flocs could be higher than that of alum flocs. And the number of settled PACl flocs could be higher than that of settled alum flocs. The effects of temperature on alum flocs and PACl flocs were different. Alum flocs size decreased at 5C. This is most likely due to the existence of monomeric aluminium species in alum aqueous solution. PACl flocs size did not change significantly at the 5C. This may be due to the existence of polymeric aluminium species in PACl aqueous solution. / February 2006

The success of surface water treatment strongly depends on the effectiveness of coagulant performance. Aluminium sulfate (alum), the most widely used coagulant in water treatment plants in Canada, is well known for its poor performance in cold water. Polyaluminium chloride (PACl), a relatively new polymeric aluminium coagulant increasingly being used in water treatment plants, is found to have many advantages over conventional alum. However, PACl hydrolysis reaction is quite complex and its action is not fully understood. In this research, a series of bench-scale jar tests with alum and PACl was conducted. Alum and PACl coagulation flocs were analyzed for the evaluation of coagulant performances at 19C and 5C for the Split Lake water treatment plant. The results of this research indicated that the settling properties of PACl flocs were superior to those of alum flocs, especially at the lower temperature. The average size of PACl flocs was relatively smaller than that of alum flocs. The density of PACl flocs could be higher than that of alum flocs. And the number of settled PACl flocs could be higher than that of settled alum flocs. The effects of temperature on alum flocs and PACl flocs were different. Alum flocs size decreased at 5C. This is most likely due to the existence of monomeric aluminium species in alum aqueous solution. PACl flocs size did not change significantly at the 5C. This may be due to the existence of polymeric aluminium species in PACl aqueous solution.

The success of surface water treatment strongly depends on the effectiveness of coagulant performance. Aluminium sulfate (alum), the most widely used coagulant in water treatment plants in Canada, is well known for its poor performance in cold water. Polyaluminium chloride (PACl), a relatively new polymeric aluminium coagulant increasingly being used in water treatment plants, is found to have many advantages over conventional alum. However, PACl hydrolysis reaction is quite complex and its action is not fully understood. In this research, a series of bench-scale jar tests with alum and PACl was conducted. Alum and PACl coagulation flocs were analyzed for the evaluation of coagulant performances at 19C and 5C for the Split Lake water treatment plant. The results of this research indicated that the settling properties of PACl flocs were superior to those of alum flocs, especially at the lower temperature. The average size of PACl flocs was relatively smaller than that of alum flocs. The density of PACl flocs could be higher than that of alum flocs. And the number of settled PACl flocs could be higher than that of settled alum flocs. The effects of temperature on alum flocs and PACl flocs were different. Alum flocs size decreased at 5C. This is most likely due to the existence of monomeric aluminium species in alum aqueous solution. PACl flocs size did not change significantly at the 5C. This may be due to the existence of polymeric aluminium species in PACl aqueous solution.

O presente trabalho avaliou o uso e a detecção de óxido de cálcio e ozônio para a inativação de cistos de Giardia spp. e oocistos de Cryptosporidium parvum presentes nos resíduos e na água de lavagem dos filtros gerados após a utilização da tecnologia de ciclo completo com flotação por ar dissolvido (coagulação, floculação, flotação e filtração) em escala de bancada, usando o cloreto de polialumínio PAC como coagulante. Para os ensaios analíticos de recuperação dos protozoários e validação do método foram utilizados as suspensões e o Easyseed® nas matrizes ALF e resíduos. A quantificação dos protozoários foi realizada pelo método de centrifugação direta com a adição de solução de dispersão detergente ICN 7X (MP BIO®) a 1,0% na amostra com a etapa de separação imunomagnética – IMS. As recuperações nos ensaios de qualidade utilizando as suspensões de protozoários foram de 19,86% ± 16,29 e 43,95% ± 11,21, para oocistos de Cryptosporidium e cistos de Giardia respectivamente na matriz ALF, enquanto que para a matriz resíduo foram de 8,16% ± 30,24 para Cryptosporidium e 32,54% ± 46,48 para Giardia. Para os ensaios de recuperação empregando o Easyseed® os valores da matriz ALF foram 2,25% ± 1,37 para Cryptosporidium e 3,75% ± 2,25 para Giardia. No resíduo, a recuperação foi de 4,5% ± 1,50 para Cryptosporidium e 49% ± 1 para Giardia. Para os ensaios com óxido de cálcio na matriz resíduo, a primeira condição com dosagem de 23 mg cal/100mL no tempo de contato de 3 dias a 25° C, não foram encontrados protozoário positivo para o teste IP (iodeto de propídeo), o que deixa esta condição satisfatória. Na segunda condição, com dosagem de 16 mg cal/100mL e tempo de contato de 3 dias a 25°C, foram encontrados protozoários negativos para IP. Para as condições de desinfecção, utilizando ozônio, com tempos de contato 5 min e 10 min e dosagens de 10 mg O3.L-1 e 7,5 mg O3.L-1, respectivamente, poucos organismos foram detectados. Portanto, destaca-se a dificuldade em avaliar a permeabilidade dos protozoários após os ensaios de desinfecção realizados. Faz-se necessário realizar novos ensaios com outras dosagens e tempos de contato. / The present work evaluated the use of calcium oxide and ozone for the inactivation of Giardia spp. and Cryptosporidium parvum oocysts present in the wastes and in the wash water of the filters obtained after the use of the complete cycle technology with dissolved air flotation (coagulation, flocculation, flotation and filtration) on a bench scale using polyaluminium chloride - PAC as a coagulant. For the analytical tests of protozoan recovery and validation of the method, suspensions and Easyseed ® were used in the ALF and residues matrices. Protozoan quantification was performed by the direct centrifugation method with the addition of detergent dispersion solution ICN 7X (MP BIO ®) at 1.0% in the sample with the immunomagnetic separation step - IMS. The recoveries in the quality assays using the protozoal suspensions were 19.86% ± 16.29 and 43.95% ± 11.21 for Cryptosporidium oocysts and Giardia cysts respectively in the ALF matrix, whereas for the residue matrix were 8.16% ± 30.24 for Cryptosporidium and 32.54 ± 46.48 for Giardia. For the recovery assays using Easyseed ® the ALF matrix values were 2.25% ± 1.37 for Cryptosporidium and 3.75% ± 2.25 for Giardia. In the residue, recovery was 4.5% ± 1.50 for Cryptosporidium and 49% ± 1 for Giardia. For the calcium oxide assays in the residue matrix, the first condition with a dosage of 23 mg cal/100mL at the contact time of 3 days at 25°C, no positive protozoan was found for the IP (propidium iodide) test, which leaves is a satisfactory condition. In the second condition with a dosage of 16 mg cal/100mL and contact time of 3 days at 25°C, negative protozoa were found for IP. For the disinfection conditions using ozone with contact times 5 min and 10 min and dosages of 10 mg O3.L-1 and 7.5 mg O3.L-1, respectively, few organisms were detected. Therefore, the difficulty in evaluating the permeability of protozoa after the disinfection tests carried out. Realization of new tests with other dosages and contact times.

O presente trabalho avaliou o uso e a detecção de óxido de cálcio e ozônio para a inativação de cistos de Giardia spp. e oocistos de Cryptosporidium parvum presentes nos resíduos e na água de lavagem dos filtros gerados após a utilização da tecnologia de ciclo completo com flotação por ar dissolvido (coagulação, floculação, flotação e filtração) em escala de bancada, usando o cloreto de polialumínio PAC como coagulante. Para os ensaios analíticos de recuperação dos protozoários e validação do método foram utilizados as suspensões e o Easyseed® nas matrizes ALF e resíduos. A quantificação dos protozoários foi realizada pelo método de centrifugação direta com a adição de solução de dispersão detergente ICN 7X (MP BIO®) a 1,0% na amostra com a etapa de separação imunomagnética – IMS. As recuperações nos ensaios de qualidade utilizando as suspensões de protozoários foram de 19,86% ± 16,29 e 43,95% ± 11,21, para oocistos de Cryptosporidium e cistos de Giardia respectivamente na matriz ALF, enquanto que para a matriz resíduo foram de 8,16% ± 30,24 para Cryptosporidium e 32,54% ± 46,48 para Giardia. Para os ensaios de recuperação empregando o Easyseed® os valores da matriz ALF foram 2,25% ± 1,37 para Cryptosporidium e 3,75% ± 2,25 para Giardia. No resíduo, a recuperação foi de 4,5% ± 1,50 para Cryptosporidium e 49% ± 1 para Giardia. Para os ensaios com óxido de cálcio na matriz resíduo, a primeira condição com dosagem de 23 mg cal/100mL no tempo de contato de 3 dias a 25° C, não foram encontrados protozoário positivo para o teste IP (iodeto de propídeo), o que deixa esta condição satisfatória. Na segunda condição, com dosagem de 16 mg cal/100mL e tempo de contato de 3 dias a 25°C, foram encontrados protozoários negativos para IP. Para as condições de desinfecção, utilizando ozônio, com tempos de contato 5 min e 10 min e dosagens de 10 mg O3.L-1 e 7,5 mg O3.L-1, respectivamente, poucos organismos foram detectados. Portanto, destaca-se a dificuldade em avaliar a permeabilidade dos protozoários após os ensaios de desinfecção realizados. Faz-se necessário realizar novos ensaios com outras dosagens e tempos de contato. / The present work evaluated the use of calcium oxide and ozone for the inactivation of Giardia spp. and Cryptosporidium parvum oocysts present in the wastes and in the wash water of the filters obtained after the use of the complete cycle technology with dissolved air flotation (coagulation, flocculation, flotation and filtration) on a bench scale using polyaluminium chloride - PAC as a coagulant. For the analytical tests of protozoan recovery and validation of the method, suspensions and Easyseed ® were used in the ALF and residues matrices. Protozoan quantification was performed by the direct centrifugation method with the addition of detergent dispersion solution ICN 7X (MP BIO ®) at 1.0% in the sample with the immunomagnetic separation step - IMS. The recoveries in the quality assays using the protozoal suspensions were 19.86% ± 16.29 and 43.95% ± 11.21 for Cryptosporidium oocysts and Giardia cysts respectively in the ALF matrix, whereas for the residue matrix were 8.16% ± 30.24 for Cryptosporidium and 32.54 ± 46.48 for Giardia. For the recovery assays using Easyseed ® the ALF matrix values were 2.25% ± 1.37 for Cryptosporidium and 3.75% ± 2.25 for Giardia. In the residue, recovery was 4.5% ± 1.50 for Cryptosporidium and 49% ± 1 for Giardia. For the calcium oxide assays in the residue matrix, the first condition with a dosage of 23 mg cal/100mL at the contact time of 3 days at 25°C, no positive protozoan was found for the IP (propidium iodide) test, which leaves is a satisfactory condition. In the second condition with a dosage of 16 mg cal/100mL and contact time of 3 days at 25°C, negative protozoa were found for IP. For the disinfection conditions using ozone with contact times 5 min and 10 min and dosages of 10 mg O3.L-1 and 7.5 mg O3.L-1, respectively, few organisms were detected. Therefore, the difficulty in evaluating the permeability of protozoa after the disinfection tests carried out. Realization of new tests with other dosages and contact times.

The aluminium content of water extracts is an important aspect for the food safety of paper board, as the content indicates the ability of the paper board material to transfer aluminium to the packaged food product. Aluminium intake in humans and its health effects have been discussed for many years as some research has seen potential links between, among other things, high aluminium levels in the brain and the development of hereditary Alzheimer's.BfR's method and recommendation is the one that is generally followed by producers around the world, as there is no common international law. The method involves leaving small pieces of the paper board in Milli-Q water for 24 hours, before a content determination of Al is made in the formed water extract. In 2021, BfR halved its recommended limit for aluminium in aqueous extracts from 2 mg/L to 1 mg/L. For Stora Enso Skoghall, this led to some of their paper board grades not meeting this limit.A specific liquid packaging board grade that previously did not meet BfR's new limit was selected and alum as a flocculant was replaced with PAC, among other things. The aim was to investigate whether the change in flocculation chemical, as well as varying dosages, could affect the Al content in water extracts and whether PAC could possibly result in a lower Al content. The method for the water extracts and their effect on the final Al content have also been investigated further. This is done by performing the BfR method with artificial tap water as well, and then comparing the Al content in these extracts.PAC as a flocculant instead of alum did not result in lower levels of Al in the water extracts. Variations in dosage and production without aluminium-containing flocculants also did not significantly affect the Al content of the extracts. The type of water used in the analysis turned out to play a major role in how much aluminium migrated from the board. All samples extracted in artificial tap water resulted in Al levels less than the 1 mg/L limit. For the majority of the samples extracted in Milli-Q water, the Al levels were instead closer to 2 mg/L. The difference in Al content between the water extracts is believed to be mainly due to differences in pH and thus varying amounts of soluble aluminium.The results showed a relatively large variation between the two external laboratories used. This is believed to be mainly due to variations in method and measuring equipment, but one must also consider the small sample size that was tested and what variations it entails.