Photo driven advanced oxidation process (AOP) with peracetic acid (PAA) has been poorly investigated in water and wastewater treatment so far. In the present work its possible use as tertiary treatment of urban wastewater to effectively minimize the release into the environment of contaminants of emerging concern (CECs) and antibiotic resistant bacteria was investigated. Different initial PAA concentrations, two light sources (sunlight and UV-C) and two different water matrices (groundwater (GW) and wastewater (WW)) were studied. Low PAA doses were found to be effective in the inactivation of antibiotic resistant Escherichia coli (AR E. coli) in GW, being UV-C driven process faster (detection limit (DL) achieved for a cumulative energy (QUV) of 0.3 kJL-1 with 0.2 mg PAA L-1) than solar driven one (DL achieved at QUV=4.4 kJL-1 with 0.2 mg PAA L-1). Really fast inactivation rates of indigenous AR E. coli were observed in WW. Higher QUV and PAA initial doses were necessary to effectively remove the three target CECs (carbamazepine (CBZ), diclofenac and sulfamethoxazole), being CBZ the more refractory one. In conclusion, photo driven AOP with PAA can be effectively used as tertiary treatment of urban wastewater but initial PAA dose should be optimized to find the best compromise between target bacteria inactivation and CECs removal as well as to prevent scavenging effect of PAA on hydroxyl radicals because of high PAA concentration.

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Water-soluble complexes cis-[Ru(bpy) 2 (PTA) 2 ]Cl 2 (1Cl 2 ), cis-[Ru(bpy) 2 (PTA) 2 ](PF 6 ) 2 [1(PF 6 ) 2 ], trans-[Ru(bpy) 2 (PTA) 2 ]-(CF 3 SO 3 ) 2 [2(CF 3 SO 3 ) 2 ], cis-[Ru(bpy) 2 (PTA)(H 2 O)](CF 3 SO 3 ) 2 [3(CF 3 SO 3 ) 2 ], cis-[Ru(bpy) 2 (PTAH)(H 2 O)](CF 3 SO 3 ) 3 ·2CF 3 SO 3 H [4(CF 3 SO 3 ) 3 ·2CF 3 SO 3 H], cis-[Ru(bpy) 2 (PTAH) 2 ](CF 3 SO 3 ) 4 · 4CF 3 SO 3 H [5(CF 3 SO 3 ) 4 ·4CF 3 SO 3 H], and trans-[Ru(bpy) 2 (PTAH) 2 ]-(CF 3 SO 3 ) 4 ·4CF 3 SO 3 H [6(CF 3 SO 3 ) 4 ·4CF 3 SO 3 H] (bpy = 2,2′-bipyridyl; PTA = 1,3,5-triaza-7-phosphaadamantane) have been synthesized and characterized by elemental analysis, NMR, and IR spectroscopy. The crystal structures of 1(PF 6 ) 2 , 2(CF 3 SO 3 ) 2 , and 3(CF 3 SO 3 ) 2 were obtained by single-crystal X-ray diffraction. Both experimental and computational techniques were utilized to perform a detailed analysis of the structural and electronic [a] Computational Details: DFT calculations at the B3LYP [35,36] level of theory were carried out with the NWCHEM 6.3 software package. [37] A Gaussian basis set of 6-31g(d,p) was used for the ligands, whereas the effective core potential LAN2DZ set was used for the ruthenium atom. Structure optimization was carried out starting from the Cartesian coordinates of the crystal structures. The COSMO model was adopted to simulate solvent effects. [19] UV absorption spectra were calculated by using time-dependent density functional theory (TD-DFT) and were obtained by convoluting the 70 lowest singlet excitation energies obtained from the Davidson solutions of the TD-DFT equations with a Gaussian distribution of FWHM = 30 nm. X-ray Structure Determination: Data for compounds were collected with a Bruker APEX CCD diffractometer (XDIFRACT service of the University of Almeria) by using graphite-monochromated Mo-K α radiation (λ = 0.7107 Å) at 150 K. The crystal parameters and other experimental details of the data collections are summarized in Table 3. The structures were solved by direct methods with SIR92, [38] refined by full-matrix least-squares methods with SHEL-XTL, [39] and refined by least-squares procedures on F 2 ; final geometrical calculations and graphical manipulations were carried out with the SHELXS-XTL package. [39] The non-hydrogen non-disordered atoms were refined with anisotropic atomic displacement parameters. All hydrogen atoms were included in calculated positions and refined by using a riding model. The quality of the resolution of

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Transformation of organic microcontaminants (OMCs) during wastewater treatments results in the generation of transformation products (TPs), which can be more persistent than parent compounds. Due to reuse of reclaimed wastewater (RWW) for crop irrigation, OMCs and TPs are released in soils being capable to translocate to crops. Furthermore, OMCs are also susceptible to transformation once they reach the soil or crops. The recalcitrant antiepileptic carbamazepine (CBZ) and some of its frequently reported TPs have been found in agricultural systems. However, there is no knowledge about the fate in reuse practices of multiple CBZ TPs that can be formed during wastewater treatment processes. For the first time, this work presents a study of the behavior of CBZ TPs generated after a conventional Ultraviolet-C (UVC) treatment in an agricultural environment. The UVC-treated water was used for the irrigation of lettuces grown under controlled conditions. The latter was compared to the fate of TPs generated in the peat and plant by irrigation with non-treated water containing CBZ. A suspect screening strategy was developed to identify the TPs using liquid chromatography coupled to quadrupole-time-of-flight (LC-QTOF-MS). The results revealed the presence of 24 TPs, 22 in UVC-treated water, 11 in peat and 9 in lettuce leaves. 4 of the TPs identified in peat (iminostilbene, TP 271B, TP 285A-B); and 3 in leaves (10-11 dihydrocarbamazepine, TP 271A-B) were not previously reported in soils or edible parts of crops, respectively. Comparing the TPs found in peat and lettuces derived from both irrigation conditions, no significant differences regarding TPs formation or occurrence were observed. UVC treatment did not contribute to the formation of different TPs than those generated by transformation or metabolism of CBZ in peat or plant material. This research improves the current knowledge on the fate of CBZ TPs in agricultural systems as a consequence of reuse practices.

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This contribution investigates the effect of solar activated persulfate and solar mild thermal heating for water disinfection (PS/solar). The basic effects of solar ultraviolet (UV) and thermal increase were separately studied for the inactivation of E. coli and E. faecalis. The process was studied in isotonic water (IW) and synthetic urban wastewater (SUWW) at bench and pilot scale (60 L-solar compound parabolic collector reactor). The thermal inactivation at 40 ºC and 0.5mM-PS shows a 3 log reduction value (LRV) for E. coli without lag phase and 5-LRV for E. faecalis with a lag phase of 1h, in 4 h of exposure. At 50 ºC the mere effect of temperature, overlaps the thermal activation of PS, being markedly fast. Effective accelerated disinfection effect by PS/solar (UVA and thermal) was observed. 6-LRV in E. coli and E. faecalis was determined for solar exposure periods of 20 min (solar dose), using 0.5 and 0.7 mM of PS in isotonic water, respectively. Longer solar exposure times were required to attain similar LRV in synthetic urban wastewater, in the presence of 25 mg/L of organic matter, i.e. 80 and 100 min (solar dose) for E. coli and E. feacalis, respectively. These results were confirmed at pilot scale, where 60 L of isotonic water were treated with 0.5 mM of PS in 50 min (solar dose). The PS/solar uses low cost chemical reagents (0.5 mM-PS) and a free source of energy (solar) to treat wastewater and achieve the high removal (6-LRV) of two model faecal indicators of water contamination, which opens a clear alternative to treat polluted water with organic matter and pathogens with implications in water-energy reclamation field.