## 3 Results and Discussion
### Study of the Kinetics of Acetamiprid Photo-Oxidation Using the Photoactive Micorparticles
The results obtained have led to the identification of compounds **a** and **b**, as well as other by-products like aldehyde hydrates, such as formaldehyde and chloronicoti-naldehyde, which have been previously reported in the literature [43, 45, 49]. Nevertheless, the decomposition into carbon dioxide, water, and nitric and hydrochloric acid was unable to be confirmed in this study. On the other hand, the kinetics of both the ADPA and Acetamiprid experiments suggest that degradation is primarily driven by singlet oxygen photocatalysis, accord  
Figure 7: Quenching of singlet molecular oxygen O\({}_{2}\)(\({}^{1}\Delta_{\beta}\)) by Acetamiprid. Compound **a** is chloronicotinic acid, and compound **b** is a secondary amine, both identified as oxidation products of Acetamiprid. ing to the reaction kinetic patterns obtained [31; 58]. Nevertheless, as supported by the literature, other reactive species, such as \(\bullet\)OH radicals, may contribute to this process, particularly in the later stages of mineralization following degradation initiated by singlet oxygen activity [54; 55; 68]. However, the literature also indicates that organic photocatalysts are unlikely to produce hydroxyl radicals [53]. While the involvement of other reactive species cannot be entirely excluded, the reaction kinetics observed in this study strongly support singlet oxygen as the primary oxidizing agent. Additionally, hydroxyl radicals are known to acidify the reaction medium, a phenomenon that was not naturally observed in this investigation. Acetamiprid Degradation Studies with P3-P4 Micorparticles as Photosensitizers in Industrial WWTP Samples  
To evaluate the degradation potential of Acetamiprid in agri-food wastewater, five effluent samples from the IWWTP were analyzed. The pesticide concentrations in these samples were notably elevated, ranging between 0.045 ppm and 0.092 ppm, according to the analytical data provided by the IWWTP manager. The sample dates coincide with peak production periods for the agri-food company. Although current regulations do not require the company to perform such analyses to determine the presence of insecticides EPs, they conduct them occasionally. Consequently, the occurrence of high Acetamiprid concentrations in the IWWTP effluent, along with the underlying causes, remains unclear. This uncertainty is likely attributed to the pesticide's seasonal application on the citrus farms that supply the company. The photosensizers P3 and P4 were utilized in the degradation tests of Acetamiprid using real water samples under two pH conditions: the actual pH of the sample and pre-adjusted at pH = 10. Table 3 presents the degradation results of Acetamiprid using P3 and P4 as photosensitizers under the two described pH conditions (reaction time of 360 min). The first-order kinetic constant obtained is also shown, along with the results for both controls: free RB and P1 (lacking RB in its structure). The degradation rates observed in the industrial effluent samples closely align with the results obtained during the initial kinetic experiments at both pH = 7-8 and pH = 10 media, using P3 and P4 as photosensitizers. As expected, degradation was more effective at pH = 10 for all samples. It is significant to note that the monitoring of Acetamiprid degradation by HPLC did not show any interference, likely due to the possible presence of organic matter. Figure 8 presents a comparison of the Acetamiprid degradation rates over time