Abstract:Stereoisomeric compositions can provide insights into sources, fate, and ecological risks of contaminants in the environment. In this study, stereoisomeric profiles of ibuprofen and iopromide were investigated in wastewater and receiving surface water of the Pearl River Delta, south China. The enantiomeric fraction (EF) of ibuprofen was 0.108-0.188 and 0.480, whereas the isomer ratio (IR) of iopromide was 1.426-1.673 and 1.737-1.898 in the influent and final effluent, respectively, suggesting stereoselective d… Show more
“…Although ibuprofen is marketed as a racemic mixture, only the active S‐(+)‐enantiomer was detected in influent wastewater samples (0.35 ± 0.09 μg l −1 ). It has been reported that R‐(−)‐ibuprofen undergoes chiral inversion during metabolism causing excess of the S‐(+)‐enantiomer in urine . This effect was reflected in this study in the higher concentrations of this enantiomer in influent wastewater.…”
Section: Resultscontrasting
confidence: 74%
“…It has been reported that R-(À)-ibuprofen undergoes chiral inversion during metabolism causing excess of the S-(+)-enantiomer in urine. [23,[35][36][37] This effect was reflected in this study in the higher concentrations of this enantiomer in influent wastewater. Interestingly, both ibuprofen metabolites were detected in influent wastewater with excess of the first eluted enantiomer (EF of carboxyibuprofen 0.83 AE 0.01; EF of 2hydroxyibuprofen 0.76 AE 0.01).…”
Section: Application To Environmental Samplesmentioning
“…Although ibuprofen is marketed as a racemic mixture, only the active S‐(+)‐enantiomer was detected in influent wastewater samples (0.35 ± 0.09 μg l −1 ). It has been reported that R‐(−)‐ibuprofen undergoes chiral inversion during metabolism causing excess of the S‐(+)‐enantiomer in urine . This effect was reflected in this study in the higher concentrations of this enantiomer in influent wastewater.…”
Section: Resultscontrasting
confidence: 74%
“…It has been reported that R-(À)-ibuprofen undergoes chiral inversion during metabolism causing excess of the S-(+)-enantiomer in urine. [23,[35][36][37] This effect was reflected in this study in the higher concentrations of this enantiomer in influent wastewater. Interestingly, both ibuprofen metabolites were detected in influent wastewater with excess of the first eluted enantiomer (EF of carboxyibuprofen 0.83 AE 0.01; EF of 2hydroxyibuprofen 0.76 AE 0.01).…”
Section: Application To Environmental Samplesmentioning
“…It can be postulated that the presence of dissolved organic matter of comparatively high concentration, as well as particulates in environmental waters will reduce EC degradation kinetics by clouding sunlight intensity. However, West and Rowland (2012) found that humic acid (a small molecular weight charged species) slowed or increased degradation rate, dependant on the specific EC investigated. Increased degradation in the presence of humic acid or nitrates can be attributed to indirect photolysis (Andreozzi et al, 2003).…”
Section: Physicochemical Processesmentioning
confidence: 97%
“…It should be noted that collated toxicological response information only gives a subjective insight into toxicity as this is highly dependent on the test species studied as ECs can cause varying toxicological responses between species type. Data obtained from: (Henschel et al, 1997;Holten Lü tzhøft et al, 1999;Wollenberger et al, 2000;Cleuvers, 2003;Ferrari et al, 2003;Pro et al, 2003;Cleuvers, 2004;Eguchi et al, 2004;Pomati et al, 2004;Cleuvers, 2005;Isidori et al, 2005a,b;Heckmann et al, 2007;Isidori et al, 2007;Kim et al, 2007;DeLorenzo and Fleming, 2008;Park and Choi, 2008;Quinn et al, 2008b;De Liguoro et al, 2009;Rosal et al, 2010;Han et al, 2010;Van den Brandhof and Montforts, 2010;Dave and Herger, 2012). EC 50 's classified as <1 mg l ¡1 ¼ very toxic to aquatic organisms, 1e10 mg l ¡1 ¼ toxic to aquatic organisms, 10e100 mg l ¡1 ¼ harmful to aquatic organisms and >100 mg l ¡1 ¼ not classified (Commission of the European Communities, 1996;Cleuvers, 2003).…”
This review identifies understudied areas of emerging contaminant (EC) research in wastewaters and the environment, and recommends direction for future monitoring. Non-regulated trace organic ECs including pharmaceuticals, illicit drugs and personal care products are focused on due to ongoing policy initiatives and the expectant broadening of environmental legislation. These ECs are ubiquitous in the aquatic environment, mainly derived from the discharge of municipal wastewater effluents. Their presence is of concern due to the possible ecological impact (e.g., endocrine disruption) to biota within the environment. To better understand their fate in wastewaters and in the environment, a standardised approach to sampling is needed. This ensures representative data is attained and facilitates a better understanding of spatial and temporal trends of EC occurrence. During wastewater treatment, there is a lack of suspended particulate matter analysis due to further preparation requirements and a lack of good analytical approaches. This results in the under-reporting of several ECs entering wastewater treatment works (WwTWs) and the aquatic environment. Also, sludge can act as a concentrating medium for some chemicals during wastewater treatment. The majority of treated sludge is applied directly to agricultural land without analysis for ECs. As a result there is a paucity of information on the fate of ECs in soils and consequently, there has been no driver to investigate the toxicity to exposed terrestrial organisms. Therefore a more holistic approach to environmental monitoring is required, such that the fate and impact of ECs in all exposed environmental compartments are studied. The traditional analytical approach of applying targeted screening with low resolution mass spectrometry (e.g., triple quadrupoles) results in numerous chemicals such as transformation products going undetected. These can exhibit similar toxicity to the parent EC, demonstrating the necessity of using an integrated analytical approach which compliments targeted and non-targeted screening with biological assays to measure ecological impact. With respect to current toxicity testing protocols, failure to consider the enantiomeric distribution of chiral compounds found in the environment, and the possible toxicological differences between enantiomers is concerning. Such information is essential for the development of more accurate environmental risk assessment.
“…[70] In addition, the degree to which heavy metal cations complex with organic materials is affected by the pH of the environment. [71,72] Additional challenges are also present when using a polymeric sensing material. Some polymeric materials may shrink or swell with varying pH, which can affect the sensitivity and selectivity of the material.…”
This paper offers a critical overview of recent advancements in aqueous sensors for heavy metals. The paper focuses on the challenges and advantages of using microelectromechanical systems (MEMS) sensors in aqueous environments, as well as technical considerations for choosing appropriate polymeric sensing materials. In addition, general considerations and recommendations are included for developing MEMS chemical sensors. These considerations centre around the chemical nature of the target analyte and the environment of the sensor application. By following these recommendations and taking the time to design a suitable sensor and sensing material for the target application instead of a trial‐and‐error approach, it is possible to save both time and cost.
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