Environmental impact of pharmaceuticals and personal care products
The environmental impact of pharmaceuticals and personal care products (PPCPs) is largely speculative. PPCPs are substances used by individuals for personal health or cosmetic reasons and the products used by agribusiness to boost growth or health of livestock. PPCPs have been detected in water bodies throughout the world. The effects of these chemicals on humans and the environment are not yet known, but to date there is no scientific evidence that they have an impact on human health.
"Pharmaceuticals", or prescription and over-the-counter medications made for human use or veterinary or agribusiness purposes, are common PPCPs found in the environment. Antibiotics, nutraceuticals (e.g., vitamins), supplements, and sexual enhancement drugs are contained in this group. "Personal care products" may include cosmetics, fragrances, menstrual care products, lotions, shampoos, soaps, toothpastes, and sunscreen. These products typically enter the environment when passed through or washed off the body and into the ground or sewer lines, or when disposed of in the trash, septic tank, or sewage system.
Traces of illicit drugs can be found in waterways and may even be carried by money.
Entry and presence in the environment
The use of pharmaceuticals and personal care products (PPCPs) is on the rise with an estimated increase from 2 billion to 3.9 billion annual prescriptions between 1999 and 2009 in the United States alone. PPCPs enter into the environment through individual human activity and as residues from manufacturing, agribusiness, veterinary use, and hospital and community use. Individuals may add PPCPs to the environment through waste excretion and bathing as well as by directly disposing of unused medications to septic tanks, sewers, or trash. Because PPCPs tend to dissolve relatively easily and do not evaporate at normal temperatures, they often end up in soil and water bodies.
Some PPCPs are broken down or processed easily by a human or animal body and/or degrade quickly in the environment . However, others do not break down or degrade easily. The likelihood or ease with which an individual substance will break down depends on its chemical makeup and the metabolic pathway of the compound.
A study by the U.S. Geological Survey report published in 2002 found detectable quantities of PPCPs in 80 percent of a sampling of 139 susceptible streams in 30 states. The most common pharmaceuticals detected were steroids and nonprescription drugs; detergents, fire retardants, pesticides, natural and synthetic hormones, and an assortment of antibiotics and prescription medications were also found. A 2006 study found detectable concentrations of 28 pharmaceutical compounds in sewage treatment plant effluents, surface water, and sediment. The therapeutic classes included antibiotics, analgesics and anti-inflammatories, lipid regulators, beta-blockers, anti-epileptics, and steroid hormones. Although most chemical concentrations were detected at low levels (nano-grams/Liter (ng/L)), there are uncertainties that remain regarding the levels at which toxicity occurs and the risks of bioaccumulation of these pharmaceutical compounds.
The scope of human exposure to pharmaceuticals and personal care products from the environment is a complex function of many factors. These factors include the concentrations, types, and distribution of pharmaceuticals in the environment; the pharmacokinetics of each drug; the structural transformation of the chemical compounds either through metabolism or natural degradation processes; and the potential bioaccumulation of the drugs. More research is needed to determine the effects on humans of long-term exposure to low levels of PPCPs. The full effects of mixtures of low concentrations of different PPCPs is also unknown.
Although research has shown that PPCPs are present in water bodies throughout the world, no studies have shown a direct impact on human health. However, the absence of empirical data cannot rule out the possibility of adverse outcomes due to interactions or long-term exposures to these substances. Because the amounts of these chemicals in the water supply may be in the parts per trillion or parts per billion, it is difficult to chemically determine the exact amounts present. Many studies have therefore been focused to determining if the concentrations of these pharmaceuticals exist at or above the accepted daily intake (ADI) at which the designed biological outcomes can occur. Most PPCPs studied have been found at levels much lower than their ADI, but some exist in the environment at some orders of magnitude greater than levels that could impart more subtle outcomes, such as behavioral or intellectual changes that are not evaluated as part of their ADI.
In addition to the growing concerns about human health risks from pharmaceutical drugs via environmental exposures, many researchers have speculated about the potential for inducing an antibiotic resistance. One study found 10 different antibiotics in sewage treatment effluents, surface water, and sediments. Some microbiologists believe that if antibiotic concentrations are higher than the minimum inhibitory concentrations (MICs) of a species of pathogenic bacteria, a selective pressure would be exerted and, as a result, antibiotic resistance would be selectively promoted. It has also been proven that at even sub-inhibitory concentrations (e.g., one-fourth of the MIC), several antibiotics are able to have an effect on gene expression (e.g., as shown for the modulation of expression of toxin-encoding genes in Staphylococcus aureus). For reference the MIC of erythromycin that is effective against 90% of lab grown Campylobacter bacteria, the most common food-borne pathogen in the United States, is 0.06 ng/mL. One study found that the average concentration of erythromycin, a commonly prescribed antibiotic, was 0.09 ng/mL in water treatment plant effluents, just above the MIC for Campylobacter. Additionally, transfer of genetic elements among bacteria has been observed under natural conditions in wastewater treatment plants, and selection of resistant bacteria has been documented in sewers receiving wastewaters from pharmaceutical plants.
The relationship between risk perception and behavior is multifaceted. Risk management is most effective once the motivation behind the behavior of disposing unused pharmaceuticals is understood. There was little correlation found between the perception of risk and knowledge regarding pharmaceutical waste according to a study conducted by Cook and Bellis in 2001. This study cautioned against the effectiveness of attempting to change the public’s behavior on these health issues by warning them of the risks associated with their actions. It is advised to take careful measures to inform the public in a way that does not impart guilt but rather public awareness. For example, a study carried out by Norlund and Garvill in Sweden (2003) that found that some people may make a personal sacrifice in terms of comfort because they feel that it would be helpful to reduce further environmental damage caused by the use of cars. Awareness of air pollution problems was a factor in their decision to take action on a more environmentally favorable choice of transportation. Thus, the goal of Bound’s project encapsulates whether the perception of risk associated with pharmaceuticals has an effect on the way in which medication is commonly disposed.
In order to conduct this study, the pharmaceuticals were grouped by their therapeutic action in order to help participants identify them. The eight therapeutic groups are listed below: antibacterials, antidepressants, antihistamines, antiepileptics, hormone treatments, and lipid regulators. Next, a survey was created to examine the disposal patterns of the participants and their perception of the existing risk or threat against the environment. Respondents were asked the following questions in part one of the survey: 1. When and how they disposed of pharmaceuticals. 2. How they perceive the risk to the environment posed by pharmaceuticals. 3. To differentiate between the risks associated with different classed of pharmaceuticals. Part two of the survey involved each of the eight pharmaceutical groups described above individually. Finally, the third part asked information about the age, sex, profession, postcode, and education of participants. The sample size of participants was precise in comparison to the actual distribution of males and females in the UK: Sample- 54.8% were female and 45.2% male vs. Actual- the UK of 51.3% female to 48.7% male. Results showed that when a medication must be discarded, 63.2% of participants throw them in a bin, 21.8% return them to a pharmacist, 11.5% and 11.5% dispose of them via the toilet/sink, while the remaining 3.5% keep them. Only half of the respondents felt like pharmaceuticals could potentially be harmful to the environment. Upon examination of factors relevant to risk perception, there was no definite link found between perception and education or income.
Dr. Bound noted that participation in altruistic activities such as Environmental Conservation groups may provide members with the ability to better grasp the effects of their actions in the environment. In regards to the aquatic environment, it is hard for one to perceive the favorable impacts of properly disposing medication. There also exists the plausibility that a person’s behavior will only be affected if there is a severe risk to themselves or humans as opposed to an environmental threat. Even though there are serious threats of pharmaceutical pollution resulting in the feminization of certain fish, they have a lower priority because they are not easily understood or experienced by the general public. In Jonathan P. Bound’s opinion, the provision of information about exactly how to go about disposing unused medication properly in conjunction with risk education may have a more positive and forceful effect.
While the full effects of most PPCPs on the environment are not understood, there is concern about the potential they have for harm because they may act unpredictably when mixed with other chemicals from the environment or concentrate in the food chain. Additionally, some PPCPS are active at very low concentrations, and are often released continuously in large or widespread quantities.
Because of the high solubility of most PPCPs, aquatic organisms are especially vulnerable to their effects. Researchers have found that a class of antidepressants may be found in frogs and can significantly slow their development. The increased presence of estrogen and other synthetic hormones in waste water due to birth control and hormonal therapies has been linked to increased feminization of exposed fish and other aquatic organisms. The chemicals within these PPCP products could either affect the feminization or masculinization of different fishes, therefore impacting their reproductive rates. In addition to being found only in waterways, the ingredients of some PPCPs can also be found in the soil. Since some of these substances take a long time or cannot be degraded biologically, they make their way up the food chain. Information pertaining to the transport and fate of these hormones and their metabolites in dairy waste disposal is still being investigated, yet research suggest that the land application of solid wastes is likely linked with more hormone contamination problems. Not only does the pollution from PPCPs affect marine ecosystems, but also those habitats that depend on this polluted water.
There are various concerns about the effects of pharmaceuticals found in surface waters and specifically the threats against rainbow trout exposed to treated sewage effluents. Analysis of these pharmaceuticals in the blood plasma of fish compared to human therapeutic plasma levels have yielded vital information providing a means of assessing risk associated with medication waste in water. In a study by Dr. Jerker Fick from Umea University  rainbow trout were exposed to undiluted, treated sewage water at three different sits in Sweden. They were exposed for a total of 14 days while 25 pharmaceuticals were measured in the blood plasma at different levels for analysis. The progestin Levonorgestrel was detected in fish blood plasma at concentrations between 8.5 and 12 ng mL-1 which exceed the human therapeutic plasma level. Studies show that the measured effluent level of Levonorgestrel in the three areas was shown to reduce the fertility of the rainbow trout.
The three sites chosen for field exposures were in located in Stockholm, Gothenburg, and Umea. They were chosen according to their varying degrees of treatment technologies, geographic locations, and size. The effluent treatment includes active sludge treatment, nitrogen and phosphorus removal (except in Umea), primary clarification, and secondary clarification. Juvenile rainbow trout were procured from Antens fiskodling AB, Sweden and Umlax AB, Sweden. The fish were exposed to aerated, undiluted, treated effluent. Since all of the sites underwent sludge treatment, it can be inferred that they are not representative of the low end of treatment efficacy. Of the 21 pharmaceuticals that were detected in the water samples, 18 were identified in the effluent, 17 in the plasma portion, and 14 pharmaceuticals were found in both effluent and plasma.
There have been studies conducted that examine concentrations of the drug Diclofenac in rainbow trout as well. This particular pharmaceutical has been found to cause damage to the kidney such as degeneration of the tubular epithelial cells and the cause of interstitial nephritis. Diclofenac is a common antiheumatic and antiphologistic drug. The drug may be improperly disposed or not fully degraded and then excreted after consumption. In surface waters, the maximum concentrations are in the range or 2 g/L (Lehmann, 2000 ). It has been determined by J. Schwaiger and his lab that rainbow trout exposed to Diclofenac for a four-week time period leads to distinct alterations in both the kidney and gills.
The result of these lethal pharmaceutical concentrations in fish is that renal lesions and damage to the gills are due to a threshold concentration of 5 g/L. As a consequence of therapeutical doses of Diclofenac there have been comparable changes in the kidney in some mammals and humans. In short term treatment of rats and dogs, alterations such as necrosis and dilation have occurred (Manocha and Venkataraman 2000). Commonly reported kidney related complications in humans such as necrosis have been reported as well.
Chemical analysis of Diclofenac residues in different organs was also examined. Even though remarkable concentrations of the drug were detected in the gills and kidney of the rainbow trout, the highest concentration was found in the liver. As opposed to Diclofenac treated humans and rats in which there was notable necrosis and inflammation in the liver, there were no detrimental histopathological alterations observed in the liver; yet, at the ultrastuctural level, Diclofenac induced cellular reactions in the liver became visible in rainbow trout after 1 g/L of exposure.
Starting in the mid-1960s, ecologists and toxicologists began to express concern about the potential adverse effects of pharmaceuticals in the water supply, but it wasn’t until a decade later that the presence of pharmaceuticals in water was well documented. Studies in 1975 and 1977 found clofibric and salicylic acids at trace concentrations in treated water. Widespread concern about and research into the effect of PPCPs largely started in the early 1990s. Until this time, PPCPs were largely ignored because of their relative solubility and containment in waterways compared to conventional pollutants like agrochemicals, industrial chemicals, and industrial waste and byproducts. Since then, a great deal of attention has been directed to the ecological and physiological risk associated with pharmaceutical compounds and their metabolites in water and the environment. In the last decade, most research in this area has focused on steroid hormones and antibiotics. There is concern that steroid hormones may act as endocrine disruptors. Some research suggests that concentrations of ethinylestradiol, an estrogen used in oral contraceptive medications and one of the most commonly prescribed pharmaceuticals, can cause endocrine disruption in aquatic and amphibian wildlife in concentrations as low as 1 ng/L.
Current research on PPCPs aims to answer these questions:
- What is the impact of exposure to low levels of PPCPs over time?
- What is the impact of exposure to mixtures of chemicals?
- Are the impacts acute (short-term) or chronic (long-term)?
- Are certain populations, such as the elderly, very young, or immuno-compromised, more vulnerable to the impacts of these compounds?
- What is the impact of PPCPs on bacterial, fungal, and aquatic life?
- Are the levels of antibiotics in the aquatic environment sufficient to promote antibiotic resistance?
- What is the impact of exposure to steroid hormones on animal and human populations?
Despite receiving attention and necessary action by regulatory agencies like FDA and the European Union, there is a lack of substantial procedures regarding impending monitoring of drug concentrations in the environment and the palpable adverse effects. In 2006 a new concept of pharmacovigilance in relation to monitoring of drugs and its impact on environmental was suggested. Pharmacoenvironmentology or ecopharmacovigilance is a branch of pharmacology and a form of pharmacovigilance (pharmecovigilance) concerning entry of chemicals or drugs into the environment after elimination from humans and animals post-therapy. It deals specifically with those pharmacological agents that have impact on the environment via elimination through living organisms subsequent to pharmacotherapy.
Ecopharmacology concerns the entry of chemicals or drugs into the environment through any route and at any concentration disturbing the balance of ecology (ecosystem), as a consequence. Ecopharmacology is a broad term that includes studies of “PPCPs” irrespective of doses and route of entry into environment.
Routes into the environment Pharmacceutical residues may reach the environment by a number of different routes. It is generally assumed (albeit hardly verified) that the production of pharmaceuticals in industrialised countries is well controlled and unharmful to the environment, due to the local legal restrictions usually required to permit production. However, a substantial fraction of the global production of pharmaceuticals takes place in low-cost production countries like India and China. Recent reports from India demonstrate that such production sites may emit very large quantities of e.g. antibiotics, yielding levels of the drugs in local surface waters higher than those found in the blood of patients under treatment. The major route for pharmaceutical residues to reach the aquatic environment is most probably by excretion from patients undergoing pharma treatment. Since many pharmaceutical substances are not metabolized in the body they may be excreted in biologically active form, usually via the urine. Furthermore, many pharmaceutical substances are not fully taken up from the intestine (following oral administration in patients) into their blood stream. The fraction not taken up into the blood stream will remain in the gut and eventually be excreted via the faeces. Hence, both urine and faeces from treated patients contain pharmaceutical residues. An additional source to environmental pollution with pharmaceuticals is improper disposal of unused or expired drug residues. In European countries take-back systems for such residues are usually in place (although not always utilized to full extent) while in e.g. the US only voluntary initiatives on a local basis exist. Proper destruction of pharma residues should yield rest products without any pharmaceutical or ecotoxic activity. Furthermore, the residues should not act as components in the environmental formation of new such products. Incineration at a high temperature (>1000 degrees Celsius) is considered to fulfil the requirements, but even following such incineration residual ashes from the incineration should be properly taken care of. Pharmaceuticals used in veterinary medicine, or as additives to animal food, pose a different problem, since they are excreted into soil or possibly open surface waters. It is wellknown that such excretions may affect terrestrial organisms directly, leading to extinction of exposed species (e.g. dung-beetles). Lipid-soluble pharma residues from veterinary use may bind strongly to soil particles, with little tendency to leak out to ground water or to local surface waters. More water-soluble residues may be washed out with rain or melting snow and reach both ground water and surface water streams.
Fate of pharmaceuticals in the sewage treatment plant Sewage treatment plants may offer a variety of techniques for diminishing the amount and harmful activity of its biological contents. Usually the sewage treatment plant (STP) is equipped with an initial mechanical separation of solid particles (socks, underwear, hygien articles etc.) appearing in the incoming water. Following this there may be filters separating finer particles either occurring in the incoming water or developing as a consequence of chemical treatment of the water with flocculating agents. Many STPs also include one or several steps of biological treatment. By stimulating the activity of various strains of microorganisms physically their activity may be promoted to degrade the organic content of the sewage by up to 90% or more. In certain cases more advanced techniques are used as well. Such techniques may comprise UV-treatment of the water, or addition of ozon. In either case, these methods will degrade organic material not taken care of by the microorganisms. Optimal treatment with such methods may destroy up to 80% or more of pharma residues in the water. A final step with acivated carbon may eliminate possible reactive degradation products from the UV or ozon treatment. Several research projects are running to optimize the use of advanced sewage treatment techniques under different conditions. The advanced techniques will increase the costs for the sewage treatment substantially. It is therefore important to define best available technique before extensive infrastructure investments are introduced on a wide basis. The fate of incoming pharmaceutical residues in the STP is unpredictable. Some substances seem to be more or less completely eliminated, while others pass the different steps in the STP unaffected. There is no systematic knowledge at hand to predict how and why this happens. Pharmaceutical residues that have been conjugated (bound to a bile acid) before being excreted from the patients may undergo de-conjugation in the STP, yielding higher levels of free pharmaceutical substance in the outlet from the STP than in its incoming water. Some pharmaceuticals with large sales volumes have not been detected in the incoming water to the STP, indicating that complete metabolism and degradation must have occurred already in the patient or during the transport of sewage from the household to the STP.
- Drug pollution
- Environmental Persistent Pharmaceutical Pollutant EPPP
- Plastic particle water pollution
- Environmental issue
- Personal care
- Water pollution
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