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Disinfection and Chlorine Disinfectants
Published in Joseph Cotruvo, Drinking Water Quality and Contaminants Guidebook, 2019
Inorganic monochloramine is increasingly being chosen as the secondary disinfectant treatment for drinking water in municipal water systems because it is less chemically reactive than free chlorine. Chloramine produces fewer and some different disinfection by-products than chlorine, and it survives longer during drinking water distribution to consumers.
Adsorption on Activated Carbon: Role of Surface Chemistry in Water Purification
Published in Jayant K. Singh, Nishith Verma, Aqueous Phase Adsorption, 2018
Ozone, chlorine dioxide, and chloramines are some of the disinfecting agents used as alternatives to replace chlorine or to be used as secondary disinfectant in order to minimize the chlorine’s adverse effects on human. Chloramines, especially monochloramine, have been used as a disinfectant in public water supplies for more than 70 years. During the last decade, chloramines have shown increased popularity among most of the water supply utilities. The main reason for selecting chloramines is that they are stable for relatively longer period and take longer to decompose in the utility’s distribution system. Also, they react less with organic compounds compared to chlorine.
Modeling the Distribution of Chloramines during Drinking Water Chloramination
Published in A. Minear Roger, L. Amy Gary, Disinfection By-Products in Water Treatment, 2017
Monochloramine is formed in drinking water treatment when aqueous chlorine combines with added ammonia. Chlorine also combines with nitrogenous organics (e.g., amino acid and proteinaceous material) to form organic chloramines. To date, little work has been done on measuring organic chloramines in treated drinking water. Gordon and colleagues8 suggested without data that organic chloramines are formed readily in water treatment.
Empirical Modeling of Bromate Formation and Chemical Control Strategies at Multiple Water Reuse Facilities Using Ozone
Published in Ozone: Science & Engineering, 2022
Nicholas Babcock, Nathanael La Breche, Keel Robinson, Aleksey N. Pisarenko
Facility C provided experimental data from Facility A and Facility D as well as itself using the following analytical procedures. For TOC analysis, samples were collected into glass vials and acidified to pH <3 with hydrochloric acid and filtered through 0.20 µm hydrophilic polypropylene filter (GHP Acrodisk, Pall Life Sciences). A Shimadzu TOC-VCSH (Shimadzu Scientific Instruments, Carlsbad, CA) total organic carbon/total nitrogen analyzer was used for quantification following SM 5310B. Bromate was determined using EPA method 326 IC-PCD. Bromide was determined using EPA method 300. Nitrate and nitrite were determined using EPA method 300 with a Thermo Scientific ICS 5000 (Thermo Fisher Scientific, Waltham, MA). Dissolved ozone was measured using the indigo method (4500-Ozone-B, (Clesceri, Greenberg and Eaton 1998)) and a Hach DR6000, UV/Vis spectrometer (Hach, Loveland, CO). Potassium indigotrisulfonate was obtained from Sigma Aldrich (St. Louis, MO), potassium monobasic phosphate, ACS grade was obtained from Fisher (Thermo Fisher Scientific, Waltham, MA). Concentrated phosphoric acid was obtained from JT Baker (Avantor Performance Materials, Phillipsburg, NJ). Hydrogen peroxide was measured following the procedure outlined in Klassen, Marchington, and McGowan (1994) using a Hach DR6000, UV/Vis spectrometer (Hach, Loveland, CO). Monochloramine was quantified using a Hach DR6000 spectrophotometer using Hach Method 10171 (Hach, Loveland, CO).
Indoor chlorine gas release in a natatorium: A case study
Published in Journal of Occupational and Environmental Hygiene, 2021
Benjamin N. Craig, Trent F. Parker, Qingsheng Wang, Michael D. Larrañaga
Chloramines include the inorganic compounds monochloramine (NH2Cl), dichloramine (NHCl2), and trichloramine (NCl3) (Jacobs et al. 2007). According to the CDC (2016), chloramines often off gas from pool water, particularly indoors, and when airborne irritate the skin, eyes, and respiratory tract similar to chlorine gas (Weng et al. 2011). Of the chloramines, trichloramine is the most volatile and is easily released into the air (Jacobs et al. 2007). When the free chlorine present within pool water contacts contaminants, including urine, saliva, sweat, and other organic materials, chloramines are formed and can spontaneously off gas into the air (Rodríguez et al. 2018). This is because these contaminants contain ammonia (NH3), which react with chlorine to generate chloramines. However, as there were likely no chloramines present in the pool water because of a lack of human activity in the newly filled and reopened pool, it is unlikely that chloramines would have interfered with the ORP readings. Thus, chloramines were excluded as a potential cause of the gas release.
Degradation of antibiotic resistance contaminants in wastewater by atmospheric cold plasma: kinetics and mechanisms
Published in Environmental Technology, 2021
Xinyu Liao, Donghong Liu, Shiguo Chen, Xingqian Ye, Tian Ding
Conventional biological wastewater treatments have been demonstrated to exhibit limited abilities to eliminate and may even increase the abundance of ARB or ARGs in the effluent [6–9]. Fars et al. [6] reported that the activated sludge, a type of biological process for water treatment, increased the proportions of antibiotic resistance faecal coliforms from 71% to 77.8%. Similar results were reported by Luczkiewicz et al. [7], who found that wastewater treatment employing an activated sludge process resulted in an increase of 5% for fluoroquinolones-resistant Enterococcus faecalis and E. faecium. Currently, the commonly used disinfection approaches for water and wastewater treatment include chlorides, chlorine dioxide, ozone, monochloramine, and ultraviolet (UV) radiation. However, not all lead to the effective elimination of ARB or ARGs [5,10]. Munir et al. [10] demonstrated that the chlorination disinfection processes resulted in no significant reduction (P > .05) of either ARB or ARGs in wastewater effluents. McKinney and Pruden [11] found that high UV doses (200–400 mJ/cm2) were required for the damage of ARGs in a phosphate-buffered saline (PBS) solution. Therefore, novel solutions are required for effective elimination of ARB and ARGs in ecosystems.