Division of the hormones based on their structural properties [1, 9-12].
\r\n\t
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Kawsar Alam",coverURL:"https://cdn.intechopen.com/books/images_new/6805.jpg",editedByType:"Edited by",editors:[{id:"199691",title:"Dr.",name:"Md. Kawsar",surname:"Alam",slug:"md.-kawsar-alam",fullName:"Md. Kawsar Alam"}],productType:{id:"1",chapterContentType:"chapter",authoredCaption:"Edited by"}}]},chapter:{item:{type:"chapter",id:"48733",title:"Endocrine Disrupting Compounds – Problems and Challenges",doi:"10.5772/60410",slug:"endocrine-disrupting-compounds-problems-and-challenges",body:'The development of new technologies, progressive urbanization, increasing consumerism, and industrial boom in developing countries has led to elevated pollution of the environment. The broad spectrum of pollutants produced and released to the environment has increased in the last few decades, including the agricultural, industrial, pharmaceutical, and plastic industries. These chemicals can be found in the individual elements of the environment, both living (biota) and non-living. Chemists very often pay attention only to chemical compounds, which are treated as substances foreign to the average chemical composition of individual elements of the environment or occur at levels higher than the so-called mean composition. However, attention should also be paid to legal aspects connected with the presence of specific pollutants in the individual elements of the environment, which are often defined as xenobiotics. Environmental research includes a broader spectrum of chemical individuals – xenobiotics – that need to be detected, identified, and determined. They can be divided into [1]:
compounds that are already subjected to legal regulations because their physicochemical properties, as well as immediate and distant toxic effects (as a result of ecotoxicological tests), and appropriate methodologies are already available and it is possible to obtain reliable information about changes in the content of these analytes in various types of environmental samples. Thus, it was possible to propose appropriate standards defining the highest concentration of a given xenobiotic in a defined environmental element. These normative values are called the
compounds that are not subjected to legal regulations yet. This group includes xenobiotics detected in the environment because new analytical methodologies were introduced into the analytical practice, which make it possible to detect and determine analytes occurring in tested environmental samples at very low levels (so-called micropollutants). It is said that the determined compounds have been so far called
The examples of the EDC groups, whose presence in the environment are both regulated and non-regulated by legal aspects, are presented in the Figure 1.
Groups of EDC pollutants subjected/not-subjected to legal regulations.
To understand endocrine disruption, the basic features and mechanisms of the endocrine system must be explained. The endocrine system consists of a number of ductless glands that secrete hormones directly into the circulatory system (to the blood) in order to regulate various functions of the body. In turn, a hormone is called a special signaling molecule that is produced by an endocrine gland. Hormone molecules travel through the blood to target distant cells and tissues to regulate physiological functions and behavior [6].
The endocrine system is made up by the following glands:
the pituitary gland at the base of the brain;
the thyroid gland in the neck;
the adrenal glands in the abdomen next to the kidneys;
the gonads (ovaries and testes) and certain parts of the pancreas;
the parathyroid gland;
the thymus.
Next to these specialized endocrine glands, many other organs and tissues have secondary endocrine functions and secrete hormones (e.g. heart, adipose tissue, muscle, liver, kidneys) [7, 8]. Just to make a story short, every system of internal secretion glands, hormones, and final organs sensitive to given stressors can be named the hormonal system. With such systems, the organism can reach and hold the homeostasis.
Hormones produce effects by acting on specialized proteins called receptors that attract and bind to specific hormones. Hormone receptors provide specificity to hormone actions, both in terms of the time and the place of hormone action. A receptor proteins superfamily consists of glucocorticoid, mineralocorticoid, androgen, estrogen, progesterone, retinoic acid, vitamin D, and thyroid receptors. Binding with ligand (antagonist or agonist)
The target of the hormonal system is the activity of estrogenic, androgenic, thyroid, and glucocorticoids hormones. Classification of the hormones based on their structural properties is presented in Table 1. The modes of action of specific signaling systems are summarized in Figure 2 [1].
EDCs are chemicals responsible for the occurrence of disturbances in the hormonal balance of the organism. This group includes both egzogenic and endogenic substances or their mixtures that impact the function of the natural hormones in the organism [13]. Taking into account complexity and importance of hormones played in organisms functioning, it must be stated that endocrine chemicals have versatile and almost unlimited cells at low concentration levels. EDCs, also called xenohormones, disturb natural hormonal balance by modifying the functioning of the hormonal system in numerous ways [13-15]. Below are specified selected processes through which EDCs may influence human beings [8, 13, 16]:
modifying hormones synthesis pathways;
hormones excretion mechanisms;
cell/tissue transport of hormones in the organism;
binding to receptors;
hormones degradation pathways.
EDCs have also imprinted in the specific mechanisms of modifying organisms functioning, just to mention [15]:
mimicking the endogenous hormones’ functioning;
antagonism with synthesis of natural hormones or their metabolism;
changes of level or activity of the hormonal receptors.
EDCs can be assigned to one of two groups [17]:
natural endocrine chemicals;
chemicals emitted to the environment as a result of anthropopression.
Mode of hormonal action in target receptor.
\n\t\t\t\t | \n\t\t\t\n\t\t\t\t | \n\t\t
Steroid hormones | \n\t\t\tThey have lipophilic characteristics and contain fragments similar to cholesterol. These belong mostly in sex hormones such as estrogens, androgens, and progesterone. Both males and females produce all these hormones, but in different quantities. | \n\t\t
Amino acids’ derivatives | \n\t\t\tThey have hydrophilic characteristics and are stored in endocrine cells until the moment it needs to be released. They connect with specific surface receptors and activate secondary signaling factors. Epinephrine is an example of such hormone. | \n\t\t
Polypeptides | \n\t\t\tThey contain amino acids varying from few to over 200 residues. These are water-soluble hormones such as insulin, growth hormone, prolactine and are stored in endocrine cells until they are needed, e.g., during metabolic regulations, lactation, growth, breeding. | \n\t\t
The first evidences of endocrine disruption in nature have been observed since the 1950s, but the source of the occuring phenomena was not known yet. Figure 3 shows the most important milestones in the development of the knowledge about endocrine disrupting micropollutants.
Currently, the studies on EDCs are spreading in all branches of science including analytical chemistry, toxicology, chemometrics (data treatment), modeling, chemical processing,
Selected milestones on Endocrine Disrupting Chemicals analysis and environmental issues.
Since the 1960s, the huge increase of the number of such scientific papers has been observed. The rate of this increase is presented in Figure 4.
Increasing number of manuscripts on EDC over the years.
There is still not enough knowledge about mechanisms, modes of action and the effects that endocrine disrupting compounds and their mixtures, which are present in the environment, have on single organisms and on whole ecosystems. That is the reason why researches in this field of expertise are being held in numerous scientific centers and laboratories all over the world. In Table 2, the above mentioned scientific units are presented. The studies conducted are aimed at:
developing new analytical methodologies and their validation;
the use of various procedures to obtain information about the content of various groups of xenobiotics in samples collected from various elements of non-living environment and biota samples.
\n\t\t\t\t | \n\t\t
Catalan Institute of Water Research (ICRA) Girona, Spain | \n\t\t
University of Saskatchewan, Department of Veterinary Biomedical Sciences and Toxicology Centre, Saskatoon, Canada | \n\t\t
Gdańsk University of Technology, Department of Analytical Chemistry | \n\t\t
University of Arizona, Department of Chemical and Environmental Engineering, Tuscon United States | \n\t\t
University of Exert, Bioscences Exeter, United Kingdom | \n\t\t
Carleton University, Department of Chemistry, Ottawa, Canada | \n\t\t
Institute of Molecular Science, Division of Molecular Environmental Endocrinology, Japan | \n\t\t
Universiteit Antwerpen, Toxicological Center, Antwerpen, Belgium | \n\t\t
Information on selected scientific units conducting research on EDCs.
Until now, there is no clear opinion in the scientific circles concerning the harmful effects of EDCs. However, it is hard to remain calm as the review of literature concerning the issues connected to environmental chemistry and ecotoxicology shows an increasing number of articles showing a relation between the presence of xenobiotics in the environment and the annually increasing rate of incidence of various kinds of neoplasms, distorted reproductive behavior, and an increasing level of feminization of specific populations at different levels of the food chain.
Even though the majority of those studies has been conducted on animals, there is evidence confirming the negative effect of even small doses of those substances have on humans [31]. The EDC group compounds are characterized by a similar structural construction to natural estrogens. Although the activity of many xenoestrogens has been estimated to be lower than the activity of the feminine sex hormone estradiol, numerous
In addition, as the latest reports from the scientific world indicate, many of these compounds may have an influence on organisms not only through receptors. The epigenetic tests conducted have confirmed that these compounds influence the process of methylation of histone proteins, influencing alterations in the molecule expression. There are many concerns regarding the fact that these contaminations are capable of crossing the placenta barrier and the blood-brain barrier, and thus, they may have a negative influence on organisms since the early stages of their lives. This fact has been confirmed in many epidemiological studies and experiments, what indicates to a strong correlation between an exposure of the mother to the activity of xenobiotics and the occurrence of neurodevelopmental disorders of her offspring, such as ADHD, autism, or alterations in behavioural development as well as impairment of cognitive functions [33]. There are many indications that show that the compound may be also responsible for the initiation of carcinogenesis, that is why studies conducted in numerous research centers are aimed at finding the relations between the presence of xenoestrogens in the human body and the frequency of incidence of neoplasms of e.g., the testicles, prostate, uterus, ovaries, and breasts [34].
Humans may be exposed to the harmful effects of the EDCs
Routes of human exposure to EDCs.
Most data about the adverse effects of endocrine disruptors present in the environment on wild aimals come from Europe and North America. Observed changes vary from very subtle, such as small changes in the physiology and sexual behavior of some species to permanently altered sexual diferentiation. Most affected are aquatic species located on the top of the food chain, but some effects have also been observed in terrestial species. Table 3 provides information concerning some health effects induced by EDCs on wildlife [5].
\n\t\t\t\t | \n\t\t\t\n\t\t\t\t | \n\t\t\t\n\t\t\t\t | \n\t\t
\n\t\t\t\t | \n\t\t\tEndometriosis | \n\t\t\tPCBs, phtalates, dioxins | \n\t\t
Fibroids | \n\t\t\tPhtalates | \n\t\t|
Interferences in endocrine signallig of pubertal timing, fecundity, fertility and menopause | \n\t\t\t\n\t\t | |
\n\t\t\t\t | \n\t\t\tTesticular cancer | \n\t\t\t\n\t\t |
Testis germ cel | \n\t\t||
Genital abnormalities in babies | \n\t\t||
Cryptorchidism | \n\t\t\tDiethylstilbestrol, pesticides | \n\t\t|
Reduced semen quality | \n\t\t\tdioxins | \n\t\t|
Hypospadias | \n\t\t\tEndocrine disrupting pesticides | \n\t\t|
Feminization | \n\t\t\tEstrogenic chemicals | \n\t\t|
\n\t\t\t\t | \n\t\t\tFewer male offsprings in human | \n\t\t\tDioxin, 1,2-dibromo-3-chloropropane | \n\t\t
EDC-related sex ratio imbalances in wild fish and molluscs | \n\t\t\t\n\t\t | |
\n\t\t\t\t | \n\t\t\tInterferences in thyroid function, including pregnant women; reduced thyroid hormones levels in blood serum in rodents | \n\t\t\tPCBs, BPA, phtalates, perfluorinated chemicals | \n\t\t
\n\t\t\t\t | \n\t\t\tBreast, endometrial, ovarian, proostate cancers | \n\t\t\tXenoestrogens (PCBs, pesticides, dioxins) | \n\t\t
Thyroid cancer | \n\t\t\tPesticides,2,3,7,8-tetrachlorodibenzo-p-dioxin | \n\t\t|
\n\t\t\t\t | \n\t\t\tAdrenocortical hyperplasia (Baltic Sea seals) | \n\t\t\tMixture of DDT and PCBs and their methyl sulfone metabolites | \n\t\t
Interfering development of the fetal adrenal cortex | \n\t\t\tPCBs | \n\t\t|
Induction delayed effects in the response to stress in animal | \n\t\t\tPCBs | \n\t\t|
\n\t\t\t\t | \n\t\t\tBone disorders, decreased bone mineral density | \n\t\t\tPCBs, DDT, hexachlorobenzene | \n\t\t
\n\t\t\t\t | \n\t\t\tObesity, diabetes | \n\t\t\tBPA, PCBs, dioxins | \n\t\t
\n\t\t\t\t \n\t\t\t\t | \n\t\t\tProstate inflammation | \n\t\t\tXenoestrogens | \n\t\t
Allergic sensitization | \n\t\t\tBPA | \n\t\t|
Lymphoma and leukemia | \n\t\t\t- | \n\t\t|
Autoimmune thyroid disease | \n\t\t\tPAHs, PCBs | \n\t\t|
Endometriosis and allergies | \n\t\t\tPhtalates, dioxins | \n\t\t|
Asthma | \n\t\t\tPhtalates | \n\t\t
Summarized information about the adverese health effects of EDCs on wildlife [7].
There is still not enough knowledge on endocrine effects on invertebrates; however, these organisms seem to be good intermediates in modeling hormonal potential toward higher organisms. There are some historical reports in which females have exhibited signs of masculinization, apparently in association with exposure to EDCs. Exposure of marine gastropods to Tributyltin (TBT), a biocide used in anti-fouling paints, provides the clearest example in invertebrates of an endocrine-mediated adverse effect caused by exposure to an environmental contaminant. Masculinization of marine gastropods exposed to TBT has resulted in worldwide declines of gastropods. The endocrine mechanism probably involves elevated androgen levels possibly through altered aromatase activity. Tributyltin-induced imposex in prosobranch female snails is a condition in which the penis “imposes” on the normal female reproductive anatomy. The associated development of the sperm duct can, in extreme cases, lead to the blockage of the oviduct of the female, resulting in sterility and population declines [1, 5, 7].
Fate and transport data interpretation is a very challenging task to perform. Although the amount of information is sufficient, it is crucial to identify critical processes and transport pathways for prioritization and screening purposes.
Analyzing the ways the endocrine active compunds enter the enviornment, it can be distinguished as an nonpoint or a one point source of pollution. Areas affected with pollution are mainly stream downs from cornfields and farm areas where different types of plant protetction products and fertilizers are used, which can contain significant quantities of pharmaceutical residue. Smaller quantities can reach the ecosystems by precipitation.
There\'s no doubt that the main source of xenoestrogene emissions to the enviornment are one point pollutuion sources. A significant part of the EDC group compounds is reaching water ecosystems with sewage.
And with that occuring, surface waters and underground waters have higher levels of concentration of these substances than in air or soil.
Residue of pharamceuticals and other substances that are biologically active coming from sources such as houses, hospitals, and production plants head to the sewer plants where they undergo different processes of water purification. Unfortunately, due to their physicochemical properties, they are resistant to biodegradation processes. This results in significant quantities of residue are not eliminated and get across to water ecosystems or with sewage sludge to the soil, groundwaters, and drinking waters. The ineptitude of widely used water purification systems has caused all the elements of the environment to be polluted by endocrine compounds. Xenobiotics, after reaching water ecosystems, undergo many different changes in chemical processes in living organisms as well as the abiotic part of the environment.
There are three environmental processes that affect the environmental fate of EDCs (as well as other pollutants). They are defined as:
Persistence – the tendency of a chemical substance or its degradation products to survive in the environment without being transformed into other forms, (measure: hydrolysis half-life, aerobic and anaerobic soil metabolism, and photolysis).
Mobility – the tendency of a chemical substance to move within environmental media or between media (measure: volatility, Henry’s law constant, Kd, Koc, groundwater ubiquitous score, aged soil column leaching, and terrestrial field dissipation studies).
Bioaccumulation – the capacity of a chemical to accumulate (be stored in tissue) in an organism as a result of uptake from all environmental sources (measure: octanol water partition coefficient, BCF, and animal metabolism).
The environmental fate of endocrine disruptors is shown schematically in Figure 6 [35].
Compounds interfereing in the endocrine balance can undergo biodegradation, photodegradation, sedimantation, elimination hydrolisys, or sorption on the matter particules suspended in water. The level on which they will be adsorbed depends on the physical and chemical properties and affinity to the particles present in water [35, 36].
Compounds included in this group, just like other types of xenobiotics, may undergo the bioaccumulation process in tissues and organs of organisms at higher trophic levels. This thesis is confirmed by data on toxaphene presented in Table 4. Toxaphene is an insecticide contained in over 670 products. Toxaphene is characterised by toxicity, stability, and ability to bioaccumulate in animals and to travel long distances. Toxaphene is poorly soluble in water, so it can be found in the air, soil, or sediments on the bottom of lakes and streams [37]. In the 1970s, toxaphene was one of the most commonly used pesticides in the world [38, 39].
\n\t\t\t\t | \n\t\t\t\n\t\t\t\t | \n\t\t
Air | \n\t\t\t0.0007 | \n\t\t
Snow | \n\t\t\t0.0009–0.002 | \n\t\t
Seawater | \n\t\t\t0.0003 | \n\t\t
Zooplankton | \n\t\t\t3.6 | \n\t\t
Arctic cod | \n\t\t\t14–46 | \n\t\t
Arctic char | \n\t\t\t44–157 | \n\t\t
Ringed seal oil | \n\t\t\t130–480 | \n\t\t
European sturgeon oil | \n\t\t\t1380–5780 | \n\t\t
Narwhal oil | \n\t\t\t2240–9160 | \n\t\t
Toxaphene concentrations in samples from various parts of non-living environment and biota accumulated in the Arctic areas of Canada [41].
Toxaphene was used for fighting pest insects feeding on cotton, grain, fruits, nuts, and vegetables. In the 1970s, fishing and hunting agencies also used toxaphene for killing fish species that were considered undesirable. It was also used for fighting ticks and other acari in domestic animals and poultry. Toxaphene is currently banned in the USA and in 57 other countries worldwide, while in other 12 countries, its use is strictly restricted. At the beginning of the 1990s, toxaphene was produced in Africa and Latin America; it is estimated that it is used in the largest quantities in Africa [37, 40].
Schematic presentation of the environmental fate of endocrine disruptors.
From a historical point of view, the instrumental techniques were first tools to determine trace organic pollutant concentration levels in the environment. With the run of time albo biological methods were introduced into the scientific routine to obtain more comprehensive and reliable information of the pollution levels of given environemtnal compartments. In Figure 7, (A and B below), basic instrumental and biological data together with their short description to present the development of tools in the field of endocrine potency determination with biological methods are presented.
(a) Classification of analytical approaches used in order to detect and determine EDCs in the environmental samples and the endocrine potency of different samples. (b) Description of selected bioassays utilized for endocrine potency determination.4.1 BIOLOGICAL METHODS
Cellular biotests are good alternative to traditional analytical procedures, as well as to immunotechniques and methods utilizing living organisms as biomarkers of exposure to EDC [91]. In these types of biotests, the yeast or human cells (e.g. cells of breast or kidney cancer) are used to determine disturbances in the run of hormonal signaling [92]. The cells can be used in unchanged form or altered with proper bioengineering methods to obtain the proper response of cells to the presence of specific chemicals belonging to EDC [93]. For example, the estrogen gene can be introduced to the yeast cells from human, fish, or other species genome. In such case, the term of estrogen equivalent concentration (EEC) finds its application in the form of the formula [42]:
where:
Numerical values of this factor determines in the relative way the endocrine character of given the chemical in relation to the endocrine potency of the reference chemical, most often estradiol or 17β-estradiol.
In this way, the endocrine potency can be described using the equation [32]:
In Table 5, there are given numerical values of EFF of selected chemicals belonging to EDC.
\n\t\t\t\t | \n\t\t\t\n\t\t\t\t | \n\t\t
Estradiol | \n\t\t\t | \n
17α-etynyloestradiol | \n\t | \n
Estrone | \n\t | \n
Bisphenol A | \n\t | \n
Nonylophenol | \n\t|
Octylophenol | \n\t | \n
Numerical values of EFF of selected chemicals belonging to EDC
In Table 6, the data concerning the analysis of various samples with bioassays is given.
\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t
1 | \n\t\tBisphenol A | \n\t\tBottled water samples | \n\t\t\n\t\t | ELISA | \n\t\t0.05 ng/cm3\n\t\t | \n\t\t0.01–1.33 ng/cm3\n\t\t | \n\t\t[59] | \n\t
2 | \n\t\tEstradiol and estrone | \n\t\tRiver water | \n\t\tExtraction on C-18 columns | \n\t\tRadioimmunoassay | \n\t\t0.3 ng/dm3\n\t\t | \n\t\t1.2–9.4 ng/dm3\n\t\t | \n\t\t[60] | \n\t
Testosterone | \n\t\t0.3 ng/dm3\n\t\t | \n\t\t>0.4 ng/dm3\n | \n|||||
Estriol | \n\tELISA | \n\t0.1 ng/dm3\n\t | \n\t>0.5 ng/dm3\n | \n||||
Ethinylestradiol | \n\t0.1 ng/dm3\n\t | \n\t>0.2 ng/dm3\n | \n|||||
3 | \n\tAlkylphenol ethoxylates | \n\tWastewater | \n\tFiltration with a glass-fiber filter, SPE (HLB) | \n\tLC-MS/MS ELISA | \n\t20–1000 | \n\t0.724–78.15 | \n\t[61] | \n
Bisphenol A | \n\t5–500 | \n\t0.08–1.55 | \n|||||
17 | \n\t0.05–1 | \n\t0.57–1.73 | \n|||||
17α-ethinylestradiol | \n\t0.12 ng/cm3\n\t | \n\t0.5–1000 ng/cm3\n\t | \n|||||
1,3,4,6,7,8-hexahydro-4,6,6,7,8,8-hexamethylcyclopenta[ | \n\t1.3 ng/g | \n\t<LOQ–62.1 ng/g | \n|||||
Musk xylene | \n\t0.5 ng/g | \n\t<LOQ–13.0 ng/g | \n|||||
Norethindrone | \n\t15 ng/dm3\n\t | \n\t- \n\t | \n|||||
Levonorgestrel | \n\t15 ng/dm3\n\t | \n||||||
Nonylphenol | \n\t1.3 ng/dm3\n\t | \n\t<LOD–118 ng/dm3\n\t | \n|||||
4 | \n\tTestosterone | \n\tRiver water | \n\tSPE (C18) | \n\tYES | \n\t- | \n\t0.8–35.5 ng/dm3\n\t | \n\t[62] | \n
Estrone, estradiol | \n\tRadioimmunoassay | \n\t- | \n\t3.2–4.3 ng/dm3\n\t | \n\t\n | |||
Estradiol | \n\tELISA | \n\t- | \n\t0.7–3.4 ng/dm3\n\t | \n||||
Ethinylestradiol | \n\t- | \n\t1.4–19.4 ng/dm3\n\t | \n|||||
5 | \n\tEstrone | \n\tSewage effluents | \n\tSPE (C18) | \n\tMCF-7 | \n\t- | \n\t70 ng/dm3\n\t | \n\t[63] | \n
6 | \n\tEstradiol | \n\tCleaned wastewaters | \n\tSPE (C18) | \n\tYES | \n\t- | \n\t1.1–11.1 ng/dm3\n\t | \n\t[64] | \n
7 | \n\t17 α-ethinilestradiol | \n\tSurface and sewage waters | \n\t\n\t | ELISA | \n\t- | \n\t0.035±0.002 μg /dm3\n\t | \n\t[65] | \n
Estradiol | \n\t- | \n\t0.085±0.010 μg/dm3\n\t | \n|||||
8 | \n\tEstrone | \n\tRiver waters | \n\tSPE (C18) | \n\tRIANA | \n\t- | \n\t0.17–10.7 μg/dm3\n\t | \n\t[57] | \n
Atrazine | \n\t- | \n\t0.35–1.47 μg/dm3\n\t | \n|||||
Isoproturon | \n\t- | \n\t0.11–2,83 μg/dm3\n\t | \n|||||
9 | \n\t17 β-Estradiol | \n\tWastewaters | \n\tSPE (C18) | \n\tYES | \n\t- | \n\t8.1 ng/dm3\n\t | \n\t[66] | \n
Estradiol | \n\t- | \n\t11.5 ng/dm3\n\t | \n|||||
p-Nonylphenol | \n\t- | \n\t55 ng/dm3\n\t | \n
Concentrations of selected EDCs determined in environmental samples using biological and instrumental methods.
Detection, identification, and quantitative determination of EDC-like chemicals are currently achieved mostly with chromatographic techniques. Prior to chromatographic separation and detection (mostly with mass spectrometry or time of flight detection), complex and time- and labor-consuming sample treatment are necessary as presented in Figure 8 (as exmple on the basis of data revision [67,68]).
The schematic presentation of selected estrogen determination in sewage samples with LC-MS.
Pre-treatment
Water and sewage samples collected for determination of endocrine disrupting compounds contain other various impurities. At this moment of sample treatment, the majority of samples is subjected to filtration to remove solid impurities. Pre-existing coagulation facilitates the filtration. Then the sulfuric acid, hydrochloric acid, methanol, or formaldehyde can be added to the samples to obtain the appropriate pH. The addition of one of these compounds also prevents the degradation of the assayed analytes. Samples are stored in darkness and low temperature, usually <4oC, in bottles made of amber glass to avoid photodegradation of analytes [69, 70].
The usual method of trace organic pollutants extraction is solid-phase extraction (SPE). The first step is filling the column-conditioning of the sorbent. After conditioning, the column is percolated with test sample. The target analytes and other compounds absorb in the sorbent. The next step is the elution of interfering compounds from the column. At the end, the target compounds are eluted with proper solvent mixtures. Solid phase extraction can be either: on-line where the extraction is directly integrated into the system of the quantitative analysis; or it may be off-line where the extraction column is not connected in any way with the gas or liquid chromatograph. In on-line SPE, full automation of the process occurs and the method is characterized with ease of application of samples and a large throughput. However, despite the higher costs off-line SPE, it is often used because when combined with GC, water must be removed totally prior to eluting analytes [70].
When choosing the appropriate sorbent for the SPE column, one has to take into account the chemical and physical properties of assayed compounds. One of the most frequently used cartridge packing is Oasis HLB. It allows to obtain high recovery of both the acidic, basic, and neutral compounds. Recovery exceeds 70%. This sorbent can be used for the large range of pH of the samples, ranging from 2–7. Lichrolut ENV+ cartridges are used when the sample has a low pH and contains polar organic compounds or when sample contains neutral drugs and its pH is neutral. Columns packed with C-18 are suitable for non-polar or moderately polar compounds. The extraction process must then be optimized: sample volume, the volume of sorbent cartridge, percolation rate, type of eluent and its volume. The elution solvent is selected depending on the properties of the compounds eluted and its elution strength.
A less frequently used method is the Solid Phase Microextraction (SPME). It depends on the distribution of the analyzed chemical compounds between the sample and the sorbent. This method is fast, moderately new, and an easy method of extraction. SPME coupled with GC content allows the study of semivolatile, volatile, and non-polar analytes. More difficult is the combination of this technique with liquid chromatography. Non-volatile compounds are not totally desorbed during the thermal desorption. SPME has many advantages thus it is more attractive than the SPE method, but has a more restricted choice of sorbent and too little sorption capacity. Therefore, the parameters of this technique are still optimized for wider application and greater sensitivity. Samples after SPE or SPME are concentrated using evaporation under a gentle nitrogen stream [70].
Another common method of extraction is liquid-liquid extraction (LLE). LLE relies on shaking the sample with an organic solvent for a specified period of time. One can perform this operation several times. The organic phase is separated from the water, and mixture of all the extracts is obtained. The resulting solution is dried, for example, using anhydrous sodium sulfite. When the sample volume is sufficiently small, determination of analytes can be started [71].
Liquid chromatography combined with tandem mass spectrometer is the most widely used analytical technique because it allows ion fragmentation that is needed for accurate and precise determination of the analytes. LC-MS/MS determines the compounds that have identical molecular weight but disparate product ions. Using MS/MS increases the selectivity and sensitivity of the method. Atmospheric pressure chemical and electrospray ionization (APCI and ESI) are modes of ionization interfaces that are the most widely used with LC-MS/MS. Low or medium polar compounds are determined by APCI, and the analysis of polar analytes is conducted using ESI. The main use of liquid chromatography is to determine non-volatile, polar, or degradable under high temperature substances. For example, beta-blockers and antibiotics can by analyzed using only LC-MS/MS [70].
One of the biggest difficulties with LC-MS/MS is interference in the matrix effects. This effect causes the strengthening or suppression of the analyte signal, thus producing erroneous results. When contaminated environmental samples are analyzed, for example wastewater, it is necessary to perform efficient clean up of samples. The process of optimizing the analytical methods, such as of liquid chromatography, involves making a series of studies to determine the parameters that give the best results for all determined substances. MS parameters are also optimized for each analyte by conducting the flow injection analysis (FIA). To obtain credible results, it is needed to optimize the separation of compounds by liquid chromatography and mass spectrometry parameters.
In case of GC-MS analysis, the matrix effects occur less frequently than during the analysis of LC-MS/MS. The disadvantage is that it is a more time-consuming technique and requires complex preparation of the sample in case of derivatization step.
As a result of derivatization of polar components, their analogs are less polar and more thermostable. It increases the sensitivity of analysis but also increases the loss of sample by performing additional operations. A negative aspect of derivatization is the use of carcinogenic and toxic reagents. Derivatization reaction should allow the detection of analytes that have polar functional groups. It is effective when the reaction occurs in a given time with 90% efficiency.
In literature there can be found many applications of GC-MS for the analysis of drugs, PAHs, PCBs, and other pollutants in water and wastewater samples [70].
In Table 7, there are presented examples of determining the EDCs in environmental samples, mainly in samples of river, drinking, surface, and sewage water. They are also determined in samples of food, air, in the tissues of the Chinese sturgeon, in house dust, and in human serum.
It can be stated that LC-MS/MS and GC-MS are the most often used techniques in determining EDCs. Other methods such as high performance liquid chromatography with fluorescence or diode array detector are less frequently used in the analysis of EDCs. The best results are given by the combination of LC-MS/MS with GC-MS.
On the basis of data collected in Table 1, it can be concluded that people and other living organisms are exposed to EDCs throughout their entire life. Even low concentrations levels of EDCs can have a significant impact on animal and human health and the existence/health state of entire populations. Many people do not realize that even these small amounts can be significantly harmful after long exposure. The concentration of some compounds from the EDC groups has decreased because their application was banned. Unfortunately, they have long half-lives, so trace amounts are present in the samples assayed decades after the release of specific chemicals.
Determination of EDCs poses many challenges and problems. Newer and more accurate analytical methods are required and need to be used by the scientific community. There are more and more articles/books about detection of EDCs in environmental samples and their harmfulness. Application of EDC should be reduced as far as possible because contamination of these compounds poses a huge risk to the environment.
\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t\t\n\t\t\t | \n\t
1 | \n\t\tTestosterone | \n\t\tHuman serum | \n\t\tLLE (diethyl ether) | \n\t\tHPLC-MS/MS | \n\t\t- | \n\t\t0.1 ng/cm3\n\t\t | \n\t\t[72] | \n\t
17-hydroxyprogesterone | \n\t\t- | \n\t\t0.1 ng/cm3\n\t\t | \n\t|||||
Cortisone and estradiol | \n\t\t- | \n\t\t0.1–50.0 ng/cm3\n\t\t | \n\t|||||
Androstenedione | \n\t\t- | \n\t\t0.1 ng/cm3\n\t\t | \n\t|||||
2 | \n\t\tDEET | \n\t\tRiver water | \n\t\tSPE | \n\t\tLC-MS/MS | \n\t\t11.6 ng/dm3\n\t\t | \n\t\t1.49–29.9 ng/dm3\n\t\t | \n\t\t[73] | \n\t
2,4-dichlorobenzoic acid | \n\t\t2.3 ng/dm3\n\t\t | \n\t\t3.24–9.35 ng/dm3\n\t\t | \n\t|||||
Erythromycin | \n\t\t13 ng/dm3\n\t\t | \n\t\t3.08–134.5 ng/dm3\n\t\t | \n\t|||||
3 | \n\t\tBisphenol A | \n\t\tDrinking and surface water | \n\t\t\n\t\t | Carbon nanotube-tyrosinase based amperometric enzymatic biosensors | \n\t\t0.02 µM | \n\t\t0.5 µg/dm3\n\t\t | \n\t\t[74] | \n\t
5 \n\t\t | \n\t\tBisphenol A | \n\t\tNatural water | \n\t\tLiChrolut RP-18 SPE | \n\t\tLC–ESI-MS | \n\t\t6.3 ng/dm3\n\t\t | \n\t\t<LOD–0,007 µg/dm3\n\t\t | \n\t\t[75] | \n\t
Estrone | \n\t\t2.5 ng/dm3\n\t\t | \n\t\t<LOD–0,022 µg/dm3\n\t\t | \n\t|||||
Desethylatrazine | \n\t\tLiChrolut RP-18 SPE | \n\t\tLC–APCI-MS | \n\t\t1.61 ng/dm3\n\t\t | \n\t\t0.002–0.003 µg/dm3\n\t\t | \n\t|||
Diuron | \n\t\t10.95 ng/dm3\n\t\t | \n\t\t0.004 µg/dm3\n\t\t | \n\t|||||
6 \n\t\t | \n\t\tEstriol | \n\t\tSurface, drinking, and waste waters | \n\t\tpH adjustment to 2 followed by SPE (HLB) | \n\t\tLC-MS/MS | \n\t\t5.0 ng/dm3\n\t\t | \n\t\t8.9–25.0 ng/dm3\n\t\t | \n\t\t[69] | \n\t
17α-ethynylestradiol | \n\t\t1.0 ng/dm3\n\t\t | \n\t\t1.3 ng/dm3\n\t\t | \n\t|||||
Estrone | \n\t\t1.0 ng/dm3\n\t\t | \n\t\t1.7–36.0 ng/dm3\n\t\t | \n\t|||||
Testosterone | \n\t\t1.0 ng/dm3\n\t\t | \n\t\t1.1 ng/dm3\n\t\t | \n\t|||||
DEET | \n\t\t1.0 ng/dm3\n\t\t | \n\t\t2.0–69 ng/dm3\n\t\t | \n\t\t\n\t | ||||
7 | \n\t\tPolyfluorinated alkyls | \n\t\tAir samples | \n\t\t\n\t\t | GC-MS | \n\t\t\n\t\t | 64–546 pg/m3\n\t\t | \n\t\t[76] | \n\t
8 | \n\t\t12 perfluorinated surfactants | \n\t\tSurface and drinking water | \n\t\tSPE | \n\t\tHPLC-MS/MS | \n\t\t\n\t\t | 2–4385 ng/dm3\n\t\t | \n\t\t[77] | \n\t
10 | \n\t\tEstrone | \n\t\tRiver water | \n\t\tSPE (HLB) Cartridge (polymer of N-vinylpyrrolidone and divinylbenzene) | \n\t\tHPLC-DAD GC-MS | \n\t\t44.0 ng/dm3\n\t\t | \n\t\t<LOD–112.9 ng/dm3\n\t\t | \n\t\t[78] | \n\t
Ethynylestradiol | \n\t\t18.0 ng/dm3\n\t\t | \n\t\t<LOD–101.9 ng/dm3\n\t\t | \n\t|||||
Daidzein | \n\t\t10.0 ng/dm3\n\t\t | \n\t\t<LOD–888.4 ng/dm3\n\t\t | \n\t|||||
4-nonylphenol | \n\t\t7.0 ng/dm3\n\t\t | \n\t\t<LOD | \n\t|||||
12 | \n\t\tEstriol | \n\t\tWastewater from a swine farm | \n\t\tSPE (N-vinylacetamide), pH adjusted to 3 | \n\t\tLC-MS/MS LC-MS | \n\t\t\n\t\t | 5200–5400 ng/dm3\n\t\t | \n\t\t[79] | \n\t
Estrone | \n\t\t\n\t\t | 2200–3000 ng/dm3\n\t\t | \n\t|||||
17α-ethinylestradiol | \n\t\t0.12 ng/cm3\n\t\t | \n\t\t0.5–1000 ng/cm3\n\t\t | \n\t|||||
Estriol | \n\t\t0.006 ng/cm3\n\t\t | \n\t\t0.35 ng/cm3\n\t\t | \n\t|||||
Bisphenol A | \n\t\t0.02 ng/cm3\n\t\t | \n\t\t0.47–0,54 ng/cm3\n\t\t | \n\t|||||
17α-ethinylestradiol | \n\t\t0.1 ng/cm3\n\t\t | \n\t\t3.57 ng/cm3\n\t\t | \n\t|||||
13 | \n\t\tHexachlorobenzene (HCB) | \n\t\tLiver, muscle, heart, gonad, stomach, intestines, adipose, gill, pancreas, kidney, gallbladder, and roe from 13 female Chinese sturgeons | \n\t\tSoxhlet extraction (dichloromethane and methanol mixture solution) | \n\t\tGC-MS | \n\t\t0.07 ng/g | \n\t\t1.6–525.0 ng/g | \n\t\t[80] | \n\t
1,1,1-trichloro-2,2-bis( | \n\t\t0.2 ng/g | \n\t\t<LOQ–480 ng/g | \n\t|||||
14 | \n\t\tEstrone | \n\t\tWastewater | \n\t\tSPE (Oasis) | \n\t\tGC-MS | \n\t\t5.6 ng/dm3\n\t\t | \n\t\t21–128.5 ng/dm3\n\t\t | \n\t\t[81] | \n\t
17β-estradiol | \n\t\t11.2 ng/dm3\n\t\t | \n\t\t10.9–224 ng/dm3\n\t\t | \n\t|||||
Bisphenol-A | \n\t\t17.4 ng/dm3\n\t\t | \n\t\t15–890 ng/dm3\n\t\t | \n\t|||||
4-tert-Octylphenol | \n\t\t8.5 ng/dm3\n\t\t | \n\t\t29–710 ng/dm3\n\t\t | \n\t|||||
15 | \n\t\tSulfadiazine | \n\t\tWaste water | \n\t\tSPE (Oasis HLB) | \n\t\tHPLC-MS/MS | \n\t\t1 ng/dm3\n\t\t | \n\t\t6–50 ng/dm3\n\t\t | \n\t\t[82] | \n\t
Estriol | \n\t\t5 ng/dm3\n\t\t | \n\t\t4648–22633 ng/dm3\n\t\t | \n\t|||||
17α- Ethynylestradiol | \n\t\t10 ng/dm3\n\t\t | \n\t\t<487 ng/dm3\n\t\t | \n\t|||||
Ethinylestradiol | \n\t\t\n\t\t | 5.7–30.8 ng/dm3\n\t\t | \n\t|||||
16 | \n\t\tAtrazine | \n\t\tWastewater | \n\t\tSPE (Oasis HLB) | \n\t\tLC-MS/MS | \n\t\t\n\t\t | 1118 ng/dm3\n\t\t | \n\t\t[83] | \n\t
17 \n\t\t | \n\t\tTestosterone | \n\t\tDrinking water | \n\t\tSPE (HLB) | \n\t\tLC-MS-ESI | \n\t\t\n\t\t | 0.116–0.214 µg/dm3\n\t\t | \n\t\t[84] | \n\t
Bis(2-ethylhexyl) phthalate | \n\t\t\n\t\t | 7–20 µg/dm3\n\t\t | \n\t|||||
17α-ethynylestradiol | \n\t\tThe CLLE extracts derivatization | \n\t\tGC-MS | \n\t\t\n\t\t | 0.073–0.831 µg/dm3\n\t\t | \n\t|||
Progesterone | \n\t\t\n\t\t | 0.11–0.199 µg/dm3\n\t\t | \n\t|||||
Sulfamethoxazole | \n\t\t1.8 ng/dm3\n\t\t | \n\t\t<410 ng/dm3\n\t\t | \n\t|||||
18 | \n\t\t4-Nonylphenol | \n\t\tWastewater | \n\t\tSPE (C18) | \n\t\tHPLC-DAD HPLC-FLD GC-MS | \n\t\t0.09 ng/dm3\n\t\t | \n\t\t3.39–169 ng/dm3\n\t\t | \n\t\t[85] | \n\t
19 | \n\t\t4-nonylphenol | \n\t\tSurface water | \n\t\tLLE (CH2Cl2) | \n\t\tHPLC-FLD | \n\t\t0.075 µg/dm3\n\t\t | \n\t\t0.08–0.39 µg/dm3\n\t\t | \n\t\t[86] | \n\t
4- | \n\t\t0.05 µg/dm3\n\t\t | \n\t\t<0.16 µg/dm3\n\t\t | \n\t|||||
20 \n\t\t | \n\t\t4-nonylphenol | \n\t\tIndoor air | \n\t\t\n\t\t | GC-MS | \n\t\t\n\t\t | 21–420 ng/m3\n\t\t | \n\t\t[87] | \n\t
Diethyl phthalatec | \n\t\t\n\t\t | 130–4300 ng/m3\n\t\t | \n\t|||||
Di-n-butyl phthalated | \n\t\t\n\t\t | 52–1100 ng/m3\n\t\t | \n\t|||||
Bis(2-ethylhexyl) phthalate | \n\t\t\n\t\t | 77–1000 ng/m3\n\t\t | \n\t|||||
Diisobuhtyl phthalate | \n\t\t\n\t\t | 11–990 ng/m3\n\t\t | \n\t|||||
Methyl paraben | \n\t\t\n\t\t | 2.9–21 ng/m3\n\t\t | \n\t|||||
4-nonylphenol | \n\t\tHousehold dust | \n\t\tSoxhlet extraction (6% diethyl ether in hexane) | \n\t\tGC-MS | \n\t\t\n\t\t | 2.58–8.68 µg/g | \n\t||
Nonylphenol monoethoxylate | \n\t\t\n\t\t | 3.36–15.6 µg/g | \n\t|||||
Benzyl butyl phthalate | \n\t\t\n\t\t | 3.87–1310 µg/g | \n\t|||||
Bis(2-ethylhexyl) phthalate | \n\t\t\n\t\t | 166.7–7700 µg/g | \n\t|||||
Metyl paraben | \n\t\t\n\t\t | 0.978–8.24 µg/g | \n\t|||||
Benzo[a]pyrene | \n\t\t\n\t\t | 0.712–18.1 µg/g | \n\t|||||
21 | \n\t\t17β-estradiol | \n\t\tSurface water, sewage sludge, and sediments. | \n\t\tSPE (C18) | \n\t\tHPLC-UV | \n\t\t\n\t\t | 1–35 ng/dm3\n\t\t | \n\t\t[88] | \n\t
Ethinyl estradiol | \n\t\t\n\t\t | 0.001–2 ng/dm3\n\t\t | \n\t|||||
22 | \n\t\tDEET | \n\t\tSurface and groundwater | \n\t\tSPE (Oasis HLB) | \n\t\tLC-MS | \n\t\t\n\t\t | 2.3–3.3 ng/dm3\n\t\t | \n\t\t[89] | \n\t
4- | \n\t\tWastewater | \n\t\tSPE (C18) | \n\t\tGC-MS | \n\t\t\n\t\t | 85 ng/dm3\n\t\t | \n\t\t[90] | \n\t|
4-nonylphenol | \n\t\t\n\t\t | 329 ng/dm3\n\t\t | \n\t|||||
Bisphenol A | \n\t\t\n\t\t | 457 ng/dm3\n\t\t | \n\t|||||
Estrone | \n\t\t\n\t\t | 63 ng/dm3\n\t\t | \n\t|||||
17α-ethynylestradiol | \n\t\t\n\t\t | 48 ng/dm3\n\t\t | \n\t
Concentrations of selected EDCs determined in environmental samples using instrumental methods.
The poor state of knowledge about the mechanisms of action and effects of EDC chemicals has forced the interdisciplinary scientific teams to intensify their work in the subject. Nowadays, many institutes are carrying out research focused on exploring the properties and metabolic pathways of EDCs and their mixtures in the environment. Good knowledge about the environmental fate, endocrine potential, and distant toxic effects of ecoestrogens will allow to estimate the levels of the pollution and minimal exposure on certain compounds. Moreover, this knowledge can be applied for upgrading the common tools used to detect and perform quantitative determination of EDCs, and can be the basis for the development of new techniques that will provide information about the composition of the sample and about its endocrine potential [94,95].
The discovery of micropollutants occurring in the environment resulted in new methodologies being put into the analytical practice. These methodologies are developed in two different directions. The first is based on methodological solutions designed to detect, identify, and determine xenobiotics that occur in various environmental samples. For this purpose, instrumental methods such as gas and liquid chromatography with mass spectrometry detection are usually used. These techniques provide reliable information about the presence, quantity, and influence of EDCs.
The second approach is to put into the analytical practice new bioanalytical methodologies. These methodologies allow estimation of the sample endocrine potential, but they do not provide information on which of the sample ingredient is responsible for causing the toxic effect. The results of the analysis of this biological response are valuable source of information for chemists and ecotoxicologists. These results can be the basis for estimating the endocrine potential of the environment exhibited by certain species. Moreover, bioanalytical techniques may be supplementary to the techniques of quantitative and qualitative determination of endocrine disrupting chemicals. It is not possible to estimate the environmental risk of EDC presence based only on the information about the sample composition. It is necessary to determine both the magnitude and how in particular the endocrine homeostasis may be impacted by xenobiotics. These tasks can be realized only by using a well-chosen bioassays battery. In the recent years there has been a significant increase in the importance of the biological methodologies in environmental research because of their numerous advantages. It is reflected in the research literature and in the increase in the number of scientific publications on this subject.
In this chapter the information about some of the estrogenic compounds, their environmental fate, and biological influence can be found. Special attention was given paid to the review of the analytical approaches used at the stage of detection and determination of EDCs in the environmental samples. Also a brief characterization of both the cellular and non-cellular bioassays is presented, as well as the information regarding the changes occurring in the bioindicators as results of being exposed to a specific ecotoxins.
The work has been co-financed by the Polish Ministry of Science and Higher Education grant no. IP2011 028071.
The International Continence Society (ICS)/International Urogynecological Association (IUGA) defines overactive bladder (OAB) as urgency with or without urge incontinence (UUI), associated with urinary frequency and nocturia in the absence of pathological (e.g. UTI, stones, bladder tumor) and metabolic factors (e.g. diabetes) [1]. The diagnosis is made by exclusion. Whether there is nerve damage or not, OAB might be classified as neurogenic or idiopathic. The prevalence of OAB is 11.8% with no significant difference between male and female and the incidence increases with age [2]. The prevalence of OAB in adults aged ≥18 years was 16% in men and 16.9% in women in the USA, and in adults aged ≥40 years, it was 15.6% for men and 17.4% for women in Europe. In Asia, the prevalence of OAB was lower, but it was still 6.0% with no differences between male and female [3].
As a result, proper understanding and management of OAB is mandatory to improve patients’ quality of life and decrease its socioeconomic burden. Behavioral therapy, bladder retraining, and pelvic floor exercise represent the first line of management of OAB. Pharmacotherapy is the second line of treatment. Anticholinergics and β3 agonists have been shown to be clinically effective in people with OAB [4]. Yet, it has many side effects such as dry mouth, dry eyes, constipation, blurred vision, dyspepsia, urine retention, and reduced cognitive function, which limit their use especially in elderly. More than 70% of patients discontinue medication within 6 months to 3 years due to side effects [5]. Refractory OAB (ROAB) develops when both behavioral therapy and oral medications become no longer effective [5]. The AUA/SUFU guidelines describe ROAB as a failure of behavioral therapy after 8–12 weeks and failure of at least one anticholinergic agent used for 4–8 weeks [6]. ROAB has an unknown prevalence rate, but it is not uncommon among the OAB population [7]. Third-line treatment should be considered when patients fulfill the ROAB diagnostic criteria. Sacral neuromodulation (SNM) and Botulinum neurotoxin-A (BoNT-A) have been recently demonstrated to be successful, with success rates reaching up to 60% and 70%, respectively [6].
BoNT-A is frequently used for cosmetic purposes and is used to treat strabismus, blepharospasm, muscle dystonia, hyperhidrosis, and migraine [8]. Carpenter was the first to prove that botulinum neurotoxin inhibits bladder contractility in rats in 1967. In 2011, BoNT-A was licensed for the treatment of urine incontinence (UI) caused by neurogenic overactive detrusors. The US Food and Drug Administration (FDA) approved it for the treatment of OAB in 2013 [9].
OAB is a chronic condition of urgency, frequency, nocturia with or without UUI. It is sub-classified into dry and wet type based on the absence or presence of the UUI. The exact cause of OAB is not well-understood. The pathophysiology varies between neurogenic, myogenic, or idiopathic factors [10]. The imbalance between the excitatory and inhibition neural pathway to the bladder is one of the underlying mechanisms. Also, the increased sensitivity of bladder muscle receptors and muscarinic receptor upregulation plays a role in OAB pathophysiology [11]. Another potential cause is the myogenic dysfunction secondary to structural or functional alteration of the detrusor smooth muscle. Idiopathic detrusor instability of undetermined underlying cause is another mechanism [10].
Proper history taking and at least a 3-day bladder diary are indicated for initial evaluation of patients in order to quantify OAB symptoms. Urodynamic evaluation is essential for establishing the diagnosis. The hallmark urodynamic feature of OAB is detrusor overactivity (DO). Yet, it may not be demonstrated in some patients due to the inability to reproduce symptoms during the urodynamic [12]. It is worth mentioning that urodynamic diagnosis has no proven predictive value for the treatment response [13]. And EAU guidelines recommended against routine urodynamic evaluation before starting the first line of treatment for uncomplicated OAB [14].
The first line of management is conservative treatment in the form of lifestyle modification (fluid restriction, decrease caffeine intake, weight reduction, and stop smoking), behavioral therapy, bladder retraining, timed voiding, and pelvic floor muscle exercise [14]. Bladder retraining and timed voiding work by setting a target time for using the toilet before it patient should not void. Once this is achieved the time can be lengthened. Thus the central control can be re-learned as in infancy. Pelvic floor muscle training; described by Kegel, aims at strengthening and rehabilitating the pelvic floor muscle, increasing its tone, and increasing urethral resistance [15].
The second recommended line of treatment is pharmacotherapy. It can be initiated together with conservative treatment or postponed till the failure of conservative treatment based on the OAB symptoms severity. The EAU and AUA guidelines recommended anticholinergics and β3 agonists as a pharmacological treatment of OAB [6, 14]. Anticholinergics are competitive muscarinic receptors antagonists. They prevent cholinergic muscarinic receptors activation in the urinary bladder and consequently reduce spontaneous detrusor muscle activity during the filling phase and decrease detrusor pressure. Many anticholinergics have been used in clinical trials and none proved to be superior to the others in OAB management. Dose escalation may be appropriate in certain patients and increases the response [16]. The efficacy of anticholinergics varies between 50% and 75%. They help to reduce urgency and UUI episodes along with reducing frequency of micturition. However, adherence to anticholinergic treatment is low and decreases over time because of lack of efficacy, adverse events, and/or cost and a significant number of patients will stop anticholinergic agents within the first 3 months [17, 18].
When anticholinergics are ineffective, non-tolerated, or contraindicated, β3 agonist (mirabegron) can be used. It activates the β-3 adrenergic receptor in the detrusor muscle in the bladder, which leads to muscle relaxation and an increase in bladder capacity helping the bladder to fill and store urine. Yet, it is not free of side effects. Tachycardia, hypertension, dyspepsia, palpitations, atrial fibrillation, joint swelling, rash, and pruritus were reported with mirabegron use [19].
Patients who are refractory to behavioral and pharmacologic therapy should be properly reevaluated. If the diagnostic criteria of ROAB are fulfilled, a third-line treatment should be offered. Third-line therapy recommended by guidelines is intradetrusor injection of BoNT-A or sacral neuromodulation [6, 14].
Botulinum toxin is a neurotoxin derived from Gram-positive, spore-producing bacteria (
BoNT-A is synthesized as a single polypeptide chain (150 kDa) which is cleaved into a light chain (50 kDa) and a heavy chain (100 kDa) held together by a fragile disulfide bond and noncovalent bonds. The available formulations of BoNT-A are BOTOX (onabotulinumtoxin A) (Allergan, United States), Dysport (abobotulinumtoxin A) (Ipsen, United Kingdom), and Xeomin (incobotulinumtoxin A) (Merz, Germany). Each formulation of BoNT-A has its own dosing regimen which is not interchangeable. BOTOX is most commonly used followed by Dysport (the former is five times more potent than the latter) [20].
Although fibroblast growth factor receptor 3 has been mentioned as a potential BoNT-A receptor, two forms of BoNT-A cell-surface receptors have been identified: gangliosides and the synaptic vesicle-associated protein 2 (SV2) family [21]. BoNT-A’s heavy chain attaches to SV2 on the nerve terminals’ surface, followed by endocytic internalization of the toxin within the nerve terminal. The toxin is broken within the synaptic vesicle after translocating into the cytoplasm, leaving the light chain of BoNT-A as the actual active moiety. BoNT-A light chain can then cleave synaptosome-associated protein (SNAP25) off the SNARE proteins, a complex protein that when intact forms the core of the neuroexocytosis machinery. This disrupts the fusion of neurotransmitter-containing vesicles with the neuronal cell membrane, inhibiting neurotransmitter release [22].
SV2-immunoreactive and SNAP25-immunoreactive nerve fibers are found in the sub-urothelium and muscle layer of the human bladder, but not in the urothelium. Almost all parasympathetic nerves express SV2 and SNAP25, while only about half of sensory and sympathetic nerves do [23]. Cleaved SNAP25 is the final product of the BoNT-A light chain’s enzymatic activity. It is regarded as an appropriate marker of BoNT-A’s action and, thus, an essential target in future research [24].
Intradetrusor injection of BoNT-A temporarily blocks the presynaptic vesicular release of acetylcholine (ACh) at the neuromuscular junction of the parasympathetic nerves supplying the detrusor muscles and decreases detrusor pressures and phasic contractions in both idiopathic and neuropathic bladders. However, patients also report a significant decrease in urgency and hence, it is hypothesized that botulinum toxin also modulates the sensory pathways [20].
BoNT-A suppresses bladder sensations by processes unrelated to its effects on ACh release. Transient receptor potential vanilloid subfamily 1 (TRPV1) and P2X3 immunoreactive fibers can be seen throughout the sub-urothelium of the human bladder [25]. BoNT-A injection reduces TRPV1 and P2X3 activity in sensory nerve fibers with subsequent reduction in the frequency of urgency episodes [26]. Also, intravesical BoNT-A injections have been demonstrated to reduce ATP and neurotrophin release from urothelial cells and increase NO release [27]. ATP has been shown to play a role in the pathophysiology of OAB by mediating the sense of bladder fullness [27].
Intradetrusor injection of BoNT-A should be offered to carefully-selected and thoroughly-counseled patients with ROAB not responding to the previous two lines of treatment. Patients should be able and willing to maintain close follow-up and frequent PVR estimation and accept the possibility of self-catheterization [6].
Patients should be given enough written and verbal peri-procedure instructions, as well as information regarding urinary tract infection (UTI) and urine retention. Prophylactic antibiotics are recommended for all patients and continue for 1–3 days postoperatively. Urinalysis should be performed before the procedure to rule out active infection. Administration of intradetrusor BoNT/A injections has been described in an office setting under local anesthesia or in the operating room with regional or general anesthesia using a flexible or rigid cystoscopy.
For idiopathic detrusor overactivity typically 100–200 units of BOTOX (diluted in 20 mL of normal saline) or 750–1000 units of Dysport have been used. BOTOX 100 U is licensed in Europe to treat OAB with persistent or refractory UUI in adults of both genders [14]. Similarly, the AUA guidelines recommended 100 U of BOTOX as a third-line of treatment of OAB [6].
There is no consensus on the ideal injection technique. The location of injections, the depth of injections, the number of injection sites, and the volume at each site vary in literature. Kuo et al. looked back at injection sites and discovered that success rates were the same whether they were in the bladder body alone, the trigone alone, or the bladder body and trigone together [28]. In a subsequent meta-analysis of OAB patients, no significant differences in efficacy between trigonal sparing and non-trigonal sparing injection techniques were found with short-term cure rates of 52.9% and 56.9%, respectively [29].
The injection depth varies as well and is influenced by the length of the needle tip (available tips range between 2 and 8 mm) used for injections. Some authors added a trace amount of indigo carmine or methylene blue to the injection solution to facilitate observation of the procedure and assessment of drug distribution [30]. Even among the same surgeons, there is likely to be some variation, and no study has determined whether sub-urothelial or intradetrusor injection is preferable. However, intradetrusor injections, as opposed to submucosal injections, with sparing of the trigone are favored. Again, there is no consensus on the number of injection sites and the dilution of the toxin but generally, 20 sites are injected and the volume per injection is usually 0.5–1 mL (Figure 1) [31].
Illustrate the technique of intra-detrusor injection of BoNT-A.
Botox is a vacuum-dried protein that must be refrigerated. The vials must be reconstituted with preservative-free saline before injection, and the combination can be kept at 2–8°C for up to 24 h.
It’s worth noting that the product contains human albumin, which should be disclosed due to some patients’ reactions to it [31].
To avoid protein denaturation, avoid rapid shaking of the vial when preparing the combination. Developing an institutional method for labeling syringes containing botulinum toxin dilutions is a significant practical consideration, especially if nurses or other personnel are engaged in its preparation [31].
Because the thickness of the detrusor muscle varies with the grade of bladder filling, puncturing the muscle appears to be very easy, especially at high bladder filling grades. Furthermore, the bladder wall between trabeculation bars might be quite thin and easily perforated. A suburothelial injection may be a viable option.
In a multicenter double-blinded randomized trial compared the efficacy of 50, 100, and 150 U onabotulinum toxin A to placebo in OAB patients, at 3 months >50% improvement in urgency and UUI was reported by 37% of the 50 U patients, 68% of 100 U patients and 58% of 150 U. Only the 100 U groups was statistically significant compared to the placebo group. Frequency was statistically significant, reduced in 100 and 150 U groups and complete continence at 3 months was significantly greater in the 100 U group (55%) and the 150 U group (50%) compared to the placebo group (11%). At five-months post-treatment, these differences were maintained [32].
A phase III trial randomized 557 OAB-wet patients; whose symptoms were not responded to anticholinergics to receive bladder wall injections with BoNT-A (100 U) or saline. At week 12, in patients treated with BoNT-A, UUI episodes were halved and the number of micturitions reduced by more than two. A total of 22.9% of the patients in the BoNT-A arm were fully dry, against 6.5% in the saline arm [33]. Tincello and colleagues published the results of the RELAX study including 240 women with refractory OAB to compare 200 U BoNT-A and placebo injections. At 6 months, voiding frequency, urgency, and incontinence episodes per day were significantly reduced in patients receiving BoNT-A injection. Continence was also significantly higher in the treatment group (31% vs. 12%, p = 0.002) with subsequent statistically significant improved patients’ QOL [34].
In early systematic review assessing the efficacy and safety of botulinum toxin in the management of OAB, Anger et al. reported that BoNT-A treatment improved incontinence episodes and patients’ QOL scores, as shown by a 15-point drop in Urinary Distress Inventory scores compared to placebo-injected patients [35]. In a recent systematic review and network meta-analysis, BoNT-A (100 U) had associated with the greatest reductions in urinary incontinence (UI) episodes, urgency episodes, and micturition frequency, and the highest odds of achieving decreases of 100% and ≥50% from baseline in UI episodes/day. In comparison to other pharmacotherapies, BoNT-A was more superior in reduction of UUI episodes, urgency, and frequency and was associated with higher odds of achieving a 100% and ≥50% decrease in UUI episodes/day than most other treatments in the network [36].
Moreover, pre-treatment with BoNT-A improved patients’ response to anticholinergic treatment. One hundred pre-treated patients with intravesical injections of 100 IU of BoNT-A and the effect faded, were randomized to receive 10 mg solifenacin and placebo for 12 weeks. After 12 weeks of follow-up, all overactive bladder symptom score items, including the total score, had improved significantly (P < 0.0001) in solifenacin group. Also, urodynamic parameters including frequency and amplitude of detrusor contractility and detrusor leak point pressure decreased significantly with increased cystometric capacity and improved incontinence quality of life parameters with solifenacin re-treatment [37]. This was explained by the possibility that repeated BoNT-A injections increased bladder capacity and restored the normal numbers and function of M3 receptors, potentially restoring patients’ responsiveness to anticholinergic drugs [37]. This was based on the clinical findings and immunohistochemical assays which evidenced that BoNT-A injections could restore the number and efficacy of intra vesical urothelial and suburothelial receptors [38].
The effects of BoNT-A injection last for 4–10 months (mean 6 months). The median time to request re-treatment in the pooled analysis of the two RCTs was 24 weeks [33, 39]. Follow-up over 3.5 years showed the consistent or increasing duration of effect for each subsequent injection, with a median of 7.5 months [14].
Intradetrusor injection of BoNT-A is still an invasive procedure and associated with a considerable incidence of adverse events. The local side effects include pain, UTI, bleeding, no benefit, need for further injections, need for temporary self-catheterization. The generalized side effects include flu-like symptoms, dry mouth, and malaise. Bauer et al. focused on side effects with botulinum toxin injection and reported that 54% of patients reported at least one side effect [40]. The side effects included urinary retention (8.9%), gross hematuria (17.9%), UTI (7.1%), dry mouth (19.6%), dysphagia (5.4%), impaired vision (5.4%), eyelid weakness (8.9%), arm weakness (8.9%), and leg weakness (7.1%). However, symptoms other than urinary retention and UTI were transient and resolved without the need for further treatment [40].
The reported rate of UTI ranged from 3.6% to 54.5% from different RCTs [6] and some reported increased rates of UTI with increases in the dose [41].
Increased PVR and the need for self-catheterization is not uncommon adverse event after botulinum toxin injection. The rate of urinary retention in published studies ranges from 5.4 to 43%, depending on how retention is defined [6, 20, 33, 39]. An interim analysis of a long-term extension study found that the proportions of patients requiring CIC remained stable at 4.6%, 4.1%, and 4.7% after one to three BoNT A treatment cycles, respectively [20]. The onset of urinary retention usually coincides with the onset of clinical efficacy, which occurs between 5 and 10 days after injection and the duration of retention varies, with some patients only requiring CIC for a few days, while others require CIC for the duration of the drug’s effects [42, 43, 44]. Multivariate analysis revealed that preoperative PVR ≥ 100 ml and preoperative bladder capacity were associated with postoperative urinary retention for the first BoNT-A treatment. Preoperative PVR, BoNT-A units injected, and retention after the first injection were all associated with an increased rate of postoperative retention in those who received a second BoNT-A treatment [45].
Mild hematuria is expected to occur transiently after the procedure due to the injection technique, but severe hematuria requiring intervention or hospitalization for bladder irrigation occurs infrequently [44]. Not all patients benefit from treatment, and many patients discontinue injections outside of clinical trials due to a lack of efficacy or intolerable side effects, such as the need for catheterization [43].
The choice between both BoNT-A and SNM for the management of ROAB is influenced by many factors. BoNT-A is a straightforward day case or outpatient procedure, which could be performed with local anesthesia or intravenous sedation. But it is still an invasive procedure. Also, due to the self-limited duration of action, reinjection every 6 months may be necessary. Whereas, SNM is more complex that necessitates a two-step procedure. However, its effect can last for 4–6 years or even longer. Currently, SNM associated risk of injury and surgical complexity are more tolerable due to the standardized and popularity of the technique. As a result, patients may prefer treatment with a longer duration [46]. Safety and effectiveness are critical factors to consider when making a decision. Efficacy and safety of BoNT-A injection and SNM are often assessed using successful treatment rates (symptoms of OAB improvement >50%) and adverse events, respectively. In A multicenter randomized trial that compared the 2-years outcome of BoNT-A and SNM, no difference in mean UUI episodes reduction was found (
The injection of BoNT-A is associated with a significant rate of side effects, particularly urinary retention. Local discomfort and infection are prevalent in SNM and are easily managed. As a result, compared to SNM, BoNT-A injection has a safety disadvantage. Both options have opposing viewpoints on their efficacy.
The suggestion would be reconsidered if we introduced cost-effectiveness. BoNT-A injection would be a cost-effective choice over a two-year period. The results of the ROSETTA randomized trial identified that two-year costs were higher for sacral neuromodulation than for BoNT-A and persisting through 5 years [49]. While at 10 years, SNM provides a considerable possibility of symptom and quality-of-life improvement and is more cost-effective compared to BoNT-A [50]. As a result, in the long run, SNM would be the better alternative.
In the case of the non-responder who was initially treated with SNM or BoNT-A injection, we do not know whether we can switch to another therapy or how effective it will be. BoNT-A can be used in SNM non-responders with a success rate of 43.4% but is associated with a high long-term discontinuation rate (55%) [51].
Furthermore, the success rate in ROAB patients who used SNM therapy after failed BoNT-A therapy was 58.5%. There was no significant difference between ROAB patients who chose SNM as replacement therapy after failed BoNT-A therapy and those who used SNM therapy as first (Table 1) [52].
Sacral neuromodulation (SNM) | Botulinum toxin (BoNT-A) | |
---|---|---|
Mechanism of action | SNM mainly functions in the central nervous system:
| BoNT-A mainly acts on the peripheral nervous system.
|
Compared to medications | Superior | Equal |
Undesirable events | Low incidence | Higher incidence, especially UTI and urine retention |
Long term stability | Long term 80% stability | Short term stability 70% of patients drop out |
Satisfaction | High maintained satisfaction | Short-term satisfaction |
Re-treatment | Less | Repeated in a less than a year |
Cost effectiveness | Long term cost effective (5 and 10 years) | Short-term cost effective (2 years) |
Comparison of the sacral neuromodulation and botulinum toxin treatment.
As mentioned before, intra-detrusor injection of BoNT-A is still an invasive procedure that requires anesthesia and is associated with specific complications especially UTI and urine retention. Also, the efficacy and safety of intra-detrusor injection are sensitive to injection volume and depth, and this issue has motivated researchers to study injection-free modes of drug delivery into the bladder [53]. Therefore, intravesical instillation rather than injection of BoNT-A seems to be a sound idea. Nevertheless, BoNT-A delivery to the bladder tissue after intravesical instillation is hampered by toxin degradation by urine proteases, dilution by urine at the time of instillation, and poor uptake due to the urothelium impermeability, which results from the watertight barrier located at the umbrella cells in the superficial layers of bladder urothelium that are augmented by glycosaminoglycan and uroplakins [54].
To overcome this barrier, intravesical instillation of BoNT-A formulated with liposome (lipo-botulinum toxin) to enhance its absorption was evaluated in two studies; one pilot study and a 2-center, double-blind, randomized, placebo-controlled trial. After 1-month, lipo-botulinum toxin instillation was associated with a statistically significant reduced urinary frequency and urgency; however, the treatment did not reduce UUI episodes. Furthermore, onabotulinum toxin complexed with liposomes did not result in urinary retention [55, 56].
Another method tested was to add a chemical agent that enhances drug delivery into the bladder tissue. Dimethyl sulfoxide (DMSO) is an organic solvent that has been used to facilitate the delivery of several anticancer drugs into animal bladders. Petrou et al. studied 25 women with ROAB that were given BoNT-A (300 U) mixed with 50% DMSO. Efficacy and toxicity were assessed at baseline, 1 and 3-months after treatment. The median number of UUI episodes decreased at 1 month (p = 0.004) and then increased back at 3 months. Also, a significant reduction in symptom scores from baseline was noted. The Impact Questionnaire short form improved from 13 to 7 at 1 month (p = 0.007), and the Urogenital Distress Inventory improved from 10 to 5 at 1 month (p = 0.003). No serious side effects or urinary retention were noted [57].
Kodama et al. stated that low energy shock waves (LESWs) increase tissue permeability and drug delivery into cells by the shear force generated by the movement of liquid relative to cells, which temporarily affects the permeability of the plasma membrane. So, it can deliver macromolecular drugs into the cell cytoplasm without toxicity [58]. In the OAB-rat model, intravesical instillation of BoNT-A plus LESW group showed statistically significant lower amplitude.
(p = 0.001) and lower frequency of detrusor contractions (p = 0.01). Histologically, combined treatments significantly reduced submucosal edema and inflammatory cell infiltrate scores. Moreover, BoNT-A plus LESW significantly increased tissue expression of antioxidant marker (superoxide dismutase) and suppressed oxidative stress marker (malondialdehyde) and inflammatory cytokines (tumor necrotic factor-α and interleukin-6) [59].
In preliminary clinical study, including 15 patients with ROAB, Intravesical instillation of 100 IU of BoNT-A was done followed by LESWs (3000 shocks over 10 min) exposure to the suprapubic area was tested. Patients were followed-up by urine analysis, urine culture, PVR, and Overactive Bladder Symptom Score (OABSS) at 1, 2, and 3 months. Patients showed statistically significant improvements in all OABSS domains and the total score after 1 and 2 months of treatment (P < 0.05). Whereas, only the nocturia domain remained significantly improved after 3 months (P = 0.02). Seven (46.6%) and 12 (80%) patients were totally dry at 1 and 2 months, respectively. Also, treated patients had no significant increase in PVR throughout the study period (P > 0.05), and none of the patients required clean intermittent catheterization [60].
Further research to optimize the procedure of injection to be less invasive, more effective, and improve the injection-free mode is mandatory and expected in the near future.
Intravesical injections of BoNT-A have been approved as third-line treatment for OAB after the failure of behavioral and pharmacotherapy with successful short-term outcomes.
Repeated injections should be put into consideration during decision-making and patient counseling.
Intravesical BoNT-A injections are associated with a significant rate of adverse events (such as increased post-void residual volume, acute urinary retention, and UTI); thus, informed consent must be given before treatment.
No consensus on the standard injection technique and dose of BoNT-A in ROAB.
Approaches to optimize the procedure techniques; to be less invasive, more effective, and with less side effects, improve the injection free mode and improve its outcome to be more durable are mandatory future perspectives.
Authors have no conflict of interest to disclose.
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Therefore, problems and their solutions also change. The industrial revolution which realized in the eighteenth century had some important impacts not only on the economic life but also on social structure. It was aimed to solve social problems and ensure prosperity through social policies, which is a multidisciplinary field, and consequently, the concept of welfare state emerged. The states, which had liberal concerns and traditional protection functions and reached a powerful position with their internationalist approaches, underwent a transformation period because of the economic and social developments which took place in the last quarter of the twentieth century. It has been subject of criticism that states increased the social expenses to satisfy the social needs and therefore caused an economic crisis in this period when the effects of globalization were discussed. 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The stabilization programs proposed by the IMF led to government guarantee of private sector external debts in the developing countries and led to a rapid increase in the public debt stock.",book:{id:"7598",slug:"public-economics-and-finance",title:"Public Economics and Finance",fullTitle:"Public Economics and Finance"},signatures:"Sibel Aybarç",authors:[{id:"286689",title:"Dr.",name:"Sibel",middleName:null,surname:"Aybarç",slug:"sibel-aybarc",fullName:"Sibel Aybarç"}]},{id:"58010",title:"Fourth Industrial Revolution: Current Practices, Challenges, and Opportunities",slug:"fourth-industrial-revolution-current-practices-challenges-and-opportunities",totalDownloads:6296,totalCrossrefCites:41,totalDimensionsCites:66,abstract:"The globalization and the competitiveness are forcing companies to rethink and to innovate their production processes following the so-called Industry 4.0 paradigm. 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