Molecularly imprinted polymer sensor systems for environmental estrogenic endocrine disrupting chemicals

Philosophiae Doctor - PhD (Chemistry)There is growing concern on endocrine disrupting compounds (EDCs). The presence of drugs in water supplies was first realized in Germany in the early 1990s when environmental scientists discovered clofibric acid. Clofibric acid has the ability to lower cholesterol in ground water below a water treatment plant. Endocrine disrupting compounds can be defined as those chemicals with the ability to alter daily functioning of the endocrine system in living organisms. There are numerous molecules that are regarded or referred to as EDCs such as but not limited to organochlorinated pesticides, industrial chemicals, plastics and plasticizers, fuels, estrogens and many other chemicals that are found in the environment or are in widespread use. 17?- estradiol is the principal estrogen found in mammals during reproductive years. Estriol is produced in large quantities during pregnancy. 17?-estradiol is the strongest, estriol the weakest. Estriol is water soluble, estrone and estradiol are not. Although estrogen is produced in women they are also at risk of over exposure to estrogen. Pesticides are extensively used today in agricultural settings to prevent and control pests. Various pesticides, including banned organochlorines (OCs) and modern non-persistent pesticides, have shown the ability to disrupt thyroid activity, disturbing the homeostasis of the thyroid system. Because these EDCs have adverse effects on health of both human and wildlife, it is imperative to develop viable costeffective analytical methods for the detection of these EDCs in complicated samples and at very low concentrations. Very high selectivity towards particular compounds is a very important property for the suitability of a detection method. This is because these compounds mostly coexist in complex matrices which makes the detection of a specific compound very challenging. It is paramount to develop highly sensitive and selective methods for the detection of these estrogens and phosphoric acid-based pesticides at trace levels

Cytochrome P450-3A4/copper-poly(propylene imine)- polypyrrole star co-polymer Nanobiosensor system for delavirdine – a non-nucleoside reverse transcriptase inhibitor HIV drug

>Magister Scientiae - MScHIV and AIDS are among the world's pandemics that pose serious concern to almost every individual in the world. With the current level of availability of anti-retroviral (ARV) drugs and the ease of accessibility of treatment in many countries such as South Africa, the disease can be controlled by suppressing the viral load of an infected individual. These anti HIV drugs such as delavirdine are metabolised by enzymes which are found in the liver microsomes, particularly those of the cytochrome P450 family. Due to the fact that the metabolic rate of a patient determines the effect of the drug, the drug could either have a beneficial or an adverse effect once it is administered. It is therefore imperative that the metabolic profile of a patient is determined at point-of-care is necessary for proper dosing of the ARV drugs. In this project a nanobiosensor system was devised and used for the determination of the metabolism of delavirdine, a non-nucleoside reverse transcriptase inhibitor (NNRTI) ARV drug. The nanobiosensor was prepared by the entrapment of the isoenzyme CYP3A4 into a pre-formed electro active carrier matrice consisting of a dendrimeric copper generation-2 poly (propylene imine)-co-polypyrrole star copolymer (Cu(G2PPI)-co-PPy). The metallo-dendrimer was used as a host for the enzyme and provided thenecessary bio-compatible environment that allowed the direct transfer of electrons between the enzyme's active centres and platinum electrode surface. Copper was the choice of metal used in the study due to its properties. Copper is a malleable, ductile and a good conductor of both heat and electricity. It is a better conductor than most metals. Silver which also belongs to group 1b in the periodic table is a better electrical conductor than copper but copper has better corrosion resistance and is a more abundant and hence it is a cheaper material to use. Cu(G2PPI)-co-PPy was prepared by the incorporation of the copper metal into the G2PPI and the electropolymerization of pyrrole onto the Cu(G2PPI). The incorporation of Cu into G2PPI was determined by FTIR which did not show the presence of the Cu but showed an increase in the intensities of the peaks after the incorporation. The surface morphology of Cu (G2PPI) was confirmed by the use of HRSEM which showed a difference in the surface morphology of the dendrimer moiety with the addition of the copper metal. The HRSEM images after Cu incorporation resulted in the change from rough surface to smooth surface with open cavities which were essential for the entrapment of the biological systems (CYP3A4). Energy dispersive spectrometry (EDS) and HRTEM were used to confirm the presence of spherically shaped copper nanoparticles in the Cu (G2PPI) and were found to have a size distribution of 12-17 nm with an average particle size of 15nm. The star copolymer (Cu(G2PPI)-co-PPy) was characterised using cyclic voltammetrywhere it was confirmed that the material was electroactive and conducting due to electron movement along the polymer chain. A diffusion co-efficient (D₀) value of 8.64 x 10⁻⁵ cm²/s was determined for the material indicating a slow electron transfer kinetics within the diffusion layer. The constructed nanobiosensor was developed using copper poly (propylene imine) – polypyrrole star copolymer, bovine serum albumin and glutaraldehyde coupled to the enzyme CYP3A4. The resultant nanobiosensor parameters include a dynamic linear range (DLR) of 0.01-0.06 nM, a limit of detection (LOD) of 0.025 nM and a sensitivity value of0.379 μA/nM

Electrochemical preparation of a MIP-glassy carbon electrode for the determination of dimethoate

In this work a dimethoate-polypyrrole (dim-PPy) MIP films were electropolymerized by cyclic voltammetry (CV) on the surface of glassy carbon electrode (GCE), using pyrrole (Py) as the monomer and dimethoate (dim) as the template. Dimethoate is electro-inactive, therefore an electroactive K3[Fe(CN)6] solution was used as probe in the CV and square wave voltammetry (SWV) for the evaluation of the performance of the imprinted (MIP) and non-imprinted (NIP) films. To investigate the analytical performance of the MIP system in the dimethoate detection, the dim-free MIP films electrode, obtained after the removal of the dimethoate, was placed in solutions containing dimethoate at different concentrations for the analyte rebinding. After the rebinding step, for the MIP films there was a decrease of the response and the current was lower than that for the dim-free MIP films. The decrease of the response could thus be used to indirectly detect the analyte quantitatively. For the NIP films, the response of K3[Fe(CN)6] was very small and showed no obvious difference with different dimethoate concentrations in the rebinding step. These results illustrated that the dim-PPy MIP film system is simple to construct and easy to operate and could be used to recognize dimethoate

Electrochemical Aptatoxisensor Responses on Nanocomposites Containing Electro-Deposited Silver Nanoparticles on Poly(Propyleneimine) Dendrimer for the Detection of Microcystin-LR in Freshwater

A sensitive and reagentless electrochemical aptatoxisensor was developed on cobalt (II) salicylaldiimine metallodendrimer (SDD–Co(II)) doped with electro-synthesized silver nanoparticles (AgNPs) for microcystin-LR (L, l-leucine; R, l-arginine), or MC-LR, detection in the nanomolar range. The GCE|SDD–Co(II)|AgNPs aptatoxisensor was fabricated with 5’ thiolated aptamer through self-assembly on the modified surface of the glassy carbon electrode (GCE) and the electronic response was measured using cyclic voltammetry (CV). Specific binding of MC-LR with the aptamer on GCE|SDD–Co(II)|AgNPs aptatoxisensor caused the formation of a complex that resulted in steric hindrance and electrostatic repulsion culminating in variation of the corresponding peak current of the electrochemical probe. The aptatoxisensor showed a linear response for MC-LR between 0.1 and 1.1 µg·L−1 and the calculated limit of detection (LOD) was 0.04 µg·L−1. In the detection of MC-LR in water samples, the aptatoxisensor proved to be highly sensitive and stable, performed well in the presence of interfering analog and was comparable to the conventional analytical techniques. The results demonstrate that the constructed MC-LR aptatoxisensor is a suitable device for routine quantification of MC-LR in freshwater and environmental samples