Pollution caused by metal elements has drawn increasing attention worldwide due to the increase of anthropogenic contaminants to the marine ecosystems. Pollution of the natural environment by metals is a serious problem because these elements are indestructible and most of them have toxic effects on living organisms, when they exceed a certain concentration. Sediments are widely used as geo-marker for monitoring and identifying the possible sources since sediment can act as sink for the pollutants. Most metals are bound in fine-grain fraction because of its high surface area-to-grain size ratio where they have a greater biological availability compared to those in larger fraction. Lying in the second trophic level in the aquatic ecosystem, shellfish species have long been known to accumulate both essential and non-essential metals. Many researchers have reported the potentiality of using mollusks, especially mussel and oyster species, as bioindicators or biomarkers for monitoring the metal contamination of the aquatic system.
- metal pollution
Recently, marine environment such as coastal and estuarine regions is contaminated by waste created by human activities containing elevated concentrations of nutrients, organic pollutants, trace metals, and radionuclide [1, 2]. Some of these chemicals are highly toxic and persistent, and these elements have a strong tendency to become concentrated in marine food webs once they enter this aquatic environment. The pollution of coastal zones near metropolitan areas, by these anthropogenic wastes, is due to the large coastal human population and the enormous amounts of sewage discharged into coastal waters [3, 4, 5, 6]. The addition of waste products into rivers, estuaries, and wetland environment (Figure 1), especially those in industrial and population centers, has led to a significant increase in this pollutant level, especially metal contamination . Accumulation of metals in surface sediments from industrial effluents and urban sewage discharged into the aquatic environment without proper treatment will easily be identified through metal spatial variations in sediments [8, 9].
Rivers can transport metals into the marine environment, and the amount of the chemical element input to the oceans depends on their levels in the river sediments, water, suspended particulate matter, and the exchange processes that occur in the estuaries . With recent industrialization and human activities (Figure 2) that happen in the coastal region, these metals are continuing to be discharged to estuarine and coastal environment through rivers, runoff, and land-based point sources where the chemical elements are produced as a result of metal refinishing by-products.
Metal concentrations in harbor or estuarine sediments usually are high due to significant anthropogenic contaminant loading carried by the upstream of tributary rivers and settled down at this area [11, 12]. The sediments itself can serve as a metal pool that can release metals to the overlying water via natural or anthropogenic chemical and physical processes, causing potential adverse health effects to organisms that live at the ecosystems [13, 14]. Moreover, marine organisms can uptake these chemical elements, which in turn enhances the potential of some elements entering into the food chain. Therefore, metal contaminations are considered by scientists as an environmental problem today in both developing and developed countries throughout the world .
Metals accumulate in the sediments through complex physical and chemical adsorption mechanisms depending on the nature of the sediment matrix and the properties of the adsorbed compounds [16, 17]. Several processes had been identified for controlling the metal concentration in sediment, such as direct adsorption by small particle of clays, adsorption of hydrous ferric and manganic oxides which may also associate with clay fraction, adsorption of natural organic substances associated with inorganic particle, and precipitation as new solid phases [18, 19]. With this unique characteristic, sediments are usually used as geo-marker for monitoring and identifying the potential pollution sources in aquatic environment. These sediment analyses are an important tool for the determination of pollutants as they sink in the bottom through different chemical constituents and can reflect the pollutant proxy in the environment. In addition, the sediments act as a useful indicator of long- and medium-term metal flux in industrialized estuaries and rivers, and they help to improve management strategies as well as to assess the success of recent pollution controls .
More than 90% of the metal compound load in marine aquatic systems is bound to suspended particulate matter and sediments . Therefore, sediments serve as a pool of metals that could be released to the overlying water from natural and anthropogenic processes such as bioturbation and dredging, resulting in potential adverse health effects toward surrounding organisms [22, 23]. Besides that, it is necessary to determine the metal contamination in estuarine ecosystem because this area is the most productive ecosystem which serves as feeding area, migration route, and nursery area of many juvenile and adult organisms from freshwater and marine water ecosystem. Due of these important to the ecosystem, effective remedial actions to minimize the pollution by metals need to be distinguished if pollution are expected occurs there .
2. Sediment as geo-marker for monitoring study
Marine sediments (Figure 3), including materials originating from the terrestrial inputs, as well as atmospheric deposition and autogenetic matter from the ocean itself, preserve a continuous record of regional and even global environmental changes, which can be employed in metal pollution evolution [25, 26]. Because of its unique characteristic, sediment always is considered as mirror of sedimentary environmental changes, which can reflect the biological, geodynamic, and geochemical processes of former conditions [27, 28]. On the other side, environmental changes are not only driven by natural forces but also by anthropogenic effects by human . Some studies had concluded that the anthropogenic impacts on the environment have led to eutrophication process in coastal zone and offshore and the interaction of the natural force and human activities has exerted great effects on the whole environmental system.
Sediments can pick up metals due to several chemical process and normally will settle down in marine aquatic environment. Because of this characteristic, sediment can act as an appropriate indicator to monitor the metal pollution. In aquatic environment, these pollutants are originated from natural and anthropogenic sources in the same manner ; thus, scientists have difficulty to identify and classify the origin of these pollutants in the environment. Therefore, to overcome these obstacles, several scientists were using sediment fraction and characterized them into several sizes to normalize the metal concentration [31, 32]. The rationale applying this approach is normally metals are associated with fine-grain fraction because this fraction has larger surface area and higher cation exchange capacity that can enhance metal adsorption . These fine sediments such as silt and clay with size less than 63 μm (Figure 3) are categorized as the most geochemically active fraction in the sediment. With this characteristic, this fraction is suitable to determine the potential pollution in the sediment (Figure 4).
Because of their large adsorption capabilities, fine-grain sediments represent a major repository for metals and a record of the temporal changes in contamination. Thus, they can be used for historical reconstruction. Although metals can occur naturally in marine environment due to their presence in local rocks, it is difficult to differentiate whether the source of the metals comes from anthropogenic or natural sources. Therefore, for better understanding about the metal behavior and distribution, it is important to distinguish between metals released from natural processes and those anthropogenic mainly introduced by human activities.
Marine sediments play a key role in the geochemical and biological processes of an estuarine ecosystem. In particular, these sediments act as sinks for toxic metals that enter the estuary. This sediment characteristic can regulate the concentration of these minerals and compounds in the water column . Marine sediment also plays a very important role in the physicochemical and ecological dynamics of metals in marine aquatic ecosystems. The physicochemical nature of sediment-bound metals is important in the bioaccumulation of aquatic organisms such as fishes and shellfish.
Sediment quality has been recognized as an important and sensitive indicator or geo-marker of environmental pollution by various scientists [35, 36] since sediments can act as an important sink for various pollutants, such as metals that had been discharged into the environment [37, 38]. Besides acting as pollution indicator, sediments are also important in the remobilization process of contaminants in aquatic environment under favorable conditions through the interaction process between waste column and surface sediments. Due to this process, scientists had developed several comprehensive methods to identify and assess the sediment contamination mainly to protect the marine aquatic organisms .
Over the last few decades, the study of sediment cores has shown to be an excellent tool for establishing the effect of anthropogenic and natural processes on depositional environments. Meanwhile, sediment cores (Figure 5) can provide chronologies of contaminant concentrations and a record of the changes in concentration of chemical indicators in the environment. During the early 1960s, sediment profiles from depositional areas were used to trace human activity, witnessed by anthropogenic contamination like phosphorus , and later in the 1970s, it was possible to distinguish radioactive isotope inputs due to nuclear tests. Metal accumulation rates in sediment cores can reflect variations in metal inputs in a given system over long periods of time. Hence, the study of sediments core provides historical record of various influences on the aquatic system by indicating both natural background levels and the man-induced accumulation of metals over an extended period of time. In addition, the dating of sediment cores using radioactive traces like 210Pb  permitted the precise quantification of the history of the inputs in a system .
3. Assessment of metal pollution level
The absolute concentration of metals in marine sediments never indicates the degree of contamination coming from either natural or anthropogenic sources because of its grain-size distribution and mineralogy characteristic [43, 44]. Normalization of metal concentrations to grain sizes, specific surface area, and reactive surface phases such as Li and Al is a common technique to remove artifacts in the data due to differences in depositional environments [45, 46, 47]. This method allows researchers to compare the contamination level directly even if the samples were collected at different locations. The most common normalization technique used is enrichment factor (EF) where this technique uses common elements such as Al, Li, and Fe as normalizer and index of geoaccumulation (Igeo) or compares the normalized concentration to average crustal abundance data [47, 48].
In order to examine to sediment status, the determined element concentrations normally were compared to the published background concentrations. Literature data on average world shale or sediment cores or sediments from pristine such as undisturbed wetlands and non-industrialized regions were analyzed to establish the background values. However, to reduce the metal variability caused by the grain sizes and mineralogy of the sediments and to identify anomalous metal contribution, geochemical normalization has been used with various degrees of success by employing conservative elements [49, 50]. Researchers have proposed various elements as normalizer, and these elements have the potential for the environmental studies. Some of them are lithium, Li [51, 52, 53]; aluminum, Al [54, 55]; scandium, Sc ; cesium, Cs [57, 58]; cobalt, Co ; and thorium, Th [60, 61]. Among all proposed normalizers, conservative elements, Li and Al, have been widely applied in marine and coastal study [62, 63, 64].
The concentration of metals in marine sediments cannot indicate the degree of contamination coming from either natural or anthropogenic sources because of grain-size distribution and mineralogy [44, 65]. Normalization of metal concentrations to sediment size, specific surface area, and reactive surface phases such as Li and Al is a common technique to remove artifacts in the data due to differences in depositional environments [46, 66]. This allows for a direct comparison to be made between contaminant levels of samples taken from different locations.
Based on the researches by several geochemists [67, 68], if an EF value is between 0 and 1.5, it is suggested that the metals may be entirely from crustal materials or natural weathering processes. If an EF is greater than 1.5, it is suggested that a significant portion of metals has arisen from non-crustal sources or anthropogenic pollution [61, 69].
Another common approach to evaluate the metal pollution in sediments is the index of geoaccumulation (Igeo) introduced by Müller  in order to determine and define metal contamination in sediments by comparing current concentrations with the background levels. Similar to metal enrichment factor, Igeo can be used as a reference to estimate the extent of metal pollution in sediments. The Igeo value is calculated by using the following equation:
where Cn is the measured concentration of the element (n) in the sediment and Bn is the geochemical background concentration of the element (n). Factor 1.5 is the correction of background matrix factor due to the lithogenic effects . The upper continental crust values of the studied metals are the same as those used in the aforementioned enrichment factor calculation . Müller  has distinguished seven classes of the Igeo from Class 0 to Class 6. The highest class (Class 6) reflects at least 100-fold environment above the background value.
|1||0 < Igeo < 1||Slightly contaminated|
|2||1 < Igeo < 1||Moderately contaminated|
|3||2 < Igeo < 1||Moderately to heavily contaminated|
|4||3 < Igeo < 1||Heavily contaminated|
|5||4 < Igeo < 1||Heavily to extremely contaminated|
|6||5 < Igeo < 1||Extremely contaminated|
Tomlinson et al.  elaborated that the application of pollution load index (PLI) provides a simple way in assessing marine and coastal sediment quality by metal pollution. This assessment is a quick tool in order to compare the pollution status of different places . PLI represents the number of times by which the metal concentrations in the sediment exceed the background concentration and gives a summative indication of the overall level of metal toxicity in a particular sample or location [74, 75]. PLI can provide some understanding to the public of the surrounding area about the quality of a component of their environment and indicates the trend spatially and temporarily . In addition, it also provides valuable information to the decision-makers toward a better management on the pollution level in the studied region.
PLI is obtained as contamination factor (CF). This CF is the quotient obtained by dividing the concentration of each metal with the background value of the metal. The PLI can be expressed from the following relation:
where n is the number of metals studied and the CF is the contamination factor. The CF can be calculated from
4. Ecological risk assessment by sediment quality guidelines
Over the last two decades, a considerable amount of research effort has been put into investigating sediment toxic threshold levels [79, 80]. As a result there are now a number of international guidelines relating to toxic concentrations as determined by field and laboratory data. The work of Long et al.  on sediment quality guidelines (SQGs) provides a useful tool for screening sediment chemical data to identify pollutants of concern and priorities problem sites (x). In their study, the toxicity range of these chemical pollutants in the sediments was estimated from experimental studies in the laboratory, observation, and measurement of these parameters in the field. The finding of the work can estimate the level of two pollutants that have high chances to give impact in adverse biological effect of 10 and 50% of biota population.
Using this approach, scientists classified the toxicity of metals into effect range low (ERL) and effect range median (ERM) concentrations . The concentration value between ERL and ERM represents the intermediate range in which this concentration can give an impact in 10–50% of the organism populations. ERL indicates the chemical pollutant can be considered to be of minimal or low concern, and the adverse effects toward organisms are infrequently observed (<10% impact on organisms population) if the concentrations are below the ERL value. On the other hand, ERM indicate that if the concentration is above this level which the significant effect can be observed in 50% or more of the organism population considered to be toxic and of significant concern.
5. GIS application in environmental study
Nowadays, the rapid developments of computer technology and geographical information system (GIS) are receiving increasing interest in environmental geochemistry study . This method is becoming popular nowadays in marine environmental pollution studies to graphically and digitally present the distribution of metals in marine environments by using GIS technique [82, 83]. The spatial interpolation methods of geometrical interpolation, trend surface analysis, and kriging method are commonly used . This base chemometric approach was applied to investigate the spatial distribution patterns of metals in marine sediment and to identify spatial human impacts on global and local scales [85, 86].
GIS is a tool for decision-making, using information stored in a geographical form, in this case, in isopleth map form. Some researchers defined major requirements and function of GIS and mentioned spatial data handling tool for solving complex geographical problems [87, 88]. This GIS approach is increasingly used in environmental pollution studies because of its ability in spatial analysis and interpolation, and spatial interpolation utilizes measured points with known values to estimate an unknown value and to visualize the spatial patterns . On the regional and national scales, the geochemical mapping of metals can be used as a tool for visualization which is enhanced by computer-aided modeling using GIS to make it easier to identify the possible locations of contaminated area. At present, joint using of GIS and chemometric approach mainly focuses on river estuary , soil , and nonpoint source identification .
6. Organisms as biomarker for monitoring study
Marine aquatic organisms can accumulate metals from various sources in their surrounding environment. The possible sources of these metals include sediments and soil erosion [93, 94], air depositions of dust and aerosol [93, 95], and discharges of wastewater [93, 94]. The accumulation of metals in marine aquatic organisms can pose a long-term burden on biogeochemical cycling in the ecosphere . Once the metals enter the food chain, they may accumulate to dangerous levels and be harmful to human health.
Shellfish species which are laying at the second trophic level in the aquatic ecosystem have long been known to accumulate both essential and nonessential metals. Many researchers have reported the potentiality of using mollusks, especially mussel and oyster species, as bioindicators or biomarkers for monitoring the metal contamination of the aquatic system [97, 98]. Besides being a biomarker for marine pollution studies, these mollusk species have also been used in ecotoxicology and toxicity studies. Individual biomonitors respond differently to different sources of bioavailable chemical elements, for example, in the solution, in sediments, or in foods. In order to conclude a complete picture of total metal bioavailability in a marine habitat, it is necessary, therefore, to use a correct biomonitor that can reflect the metal bioavailability in all available potential sources . Such comparative use of different biomonitors should allow identification of the particular source of the contaminant elements  (Figure 6).
Metal accumulation in marine aquatic organisms depended on several factors, including the environmental concentrations of metals in water and sediments; the species of organisms; and body size and age of the marine organisms. Different concentrations of metal can also be found in different organs (stomach, gill, muscle, tissue) in the same biological sample [101, 102]. However, scientists mainly focused on the general metal burden in shellfish species such as oyster and mussel and the potential major pathways for metal contaminant in the coastal environment.
7. Choice of biomonitors for environmental study
Aquatic organisms can transport pollutants and contaminants into, within, and out of the marine aquatic ecosystem. These organisms can ingest the pollutants via water and food and inhale them as they breathe and during feeding process . When the pollutants enter the organism body, some contaminants can quickly pass through several organs; however, some may be absorbed and accumulated in organism tissues, particularly fatty tissues . Certain contaminants such as mercury and PCBs are easily dissolve in organism fats and oils but do not dissolve in water. Due to the organism metabolism process, bioaccumulation process can be clearly seen in carnivorous animals in higher tropic of food chain, ranging from big organism such as fishes and to human .
The choice of a suitable biomonitor needs to consider the potential sources of metals to the organism. For example, sea grass not in contact with sediments, therefore, will take up metals from dissolved sources only . Suspension feeders take up metals both directly from seawater and from the suspended particles collected during feeding. Thus, mussels, oysters, and barnacles are all candidates as suspension feeding biomonitors, and a careful choice will differentiate between suspended particles of different size ranges. As a generalization, sessile barnacles, but not stalked barnacles, have evolved micro-feeding, using the first thoracic legs to filter small suspended particles which would pass through the setae of the expanded cirral net formed by the more posterior thoracic legs .
Deposit feeding bivalves will reflect the bioavailability of metals in the surrounding water via respiratory currents but also metal bioavailability in newly deposited particles, for they suck up such particles via the inhalant siphon during feeding . Some bivalves are protected by the shell from contact with the interstitial water of the sediment, a protection not offered, for example, to a sediment burrowing polychaete, the soft epidermis of which may be bathed directly by interstitial water with a redox potential possibly very different from that of the overlying water .
Sedentary organism or those fixed in one spot
Easy to identify the species
Available for all the time
Large enough to provide sufficient sample
Resistant to handle the organisms’ stress during test preparation
Adapt to environmental variations in physicochemical parameters such as salinity and temperature
8. Organisms as laboratory testing organisms
Besides using the organisms as a biomarker for metal pollution studies in the field, mollusk species also have been used in ecotoxicology and toxicity studies in the laboratory. Several criteria had been set in order to choose suitable organisms as testing organisms. Despite that, in order to achieve the objectives, these testing organisms should fulfill several criteria as follows:
Organisms should be commercially important and sensitive to the environment.
Organism must be easy to obtain and maintain in the laboratory.
Biology, feeding behavior, and their characteristic of the organism must be known.
Organism must be healthy and free from disease.
Organisms should be acclimatized for at least 2 weeks before use.
Mortality of organism in control tank must be less than 10%. If more than 10% mortality, the testing should be repeated.
Authors wish to express their gratitude to the metallic element research group researcher that contributes to the chapter content. Also thanks to the School of Marine and Environmental Sciences for funding the group to run the project and Oceanography Laboratory, PPSMS, for providing the facilities during the laboratory analysis.
Conflict of interest
The authors certify that they have no conflict of interest during preparation of this chapter.
Thanks to the School of Marine and Environmental Sciences, Universiti Malaysia Terengganu, that provided us the facilities to run our research project related to metal pollution.
Clark MW, Davies-McConchie F, McConchie D, Birch GF. Selective chemical extraction and grain size normalisation for environmental assessment of anoxic sediments: Validation of an integrated procedure. Science of the Total Environment. 2000; 258(3):149-170
Kennish MJ. Environmental threats and environmental future of estuaries. Environmental Conservation. 2000; 29(1):78-107
Bothner MH, Casso MA, Rendigs RR, Lamothe PJ. The effect of the new Massachustts Bay sewage outfall on the concentrations of metals and bacterial spores in nearby bottom and suspended sediments. Marine Pollution Bulletin. 2002; 44(10):1063-1070
Matthai C, Birth G, Bickford G. Anthropogenic trace metals in sediment and settling particulate matter on a high-energy continental shelf (Sydney, Australia). Marine Environmental Research. 2002; 54(2):99-127
Sadiq M. Metal contamination in sediments from a desalination plant effluent outfall area. The Science of the Total Environment. 2002; 287(1-2):37-44
Bay SM, Zeng EY, Lorenson TD, Tran K, Alexander C. Temporal and spatial distributions of contaminants in sediments of Santa Monica Bay, California. Marine Environmental Research. 2003; 56(1-2):255-276
Jayaprakash M, Srinivasalu S, Jonathan MP, Ram-Mohan V. A baseline study of physico-chemical parameters and trace metals in waters of Ennore Creek, Chennai, India. Marine Pollution Bulletin. 2005; 50(5):583-589
Baptista Neto JA, Smith BJ, McAllister JJ. Heavy metal concentrations in surface sediments in a nearshore environment, Jurujuba Sound, Southeast Brazil. Environmental Pollution. 2000; 109(1):1-9
Dauvalter V, Rognerud S. Heavy metal pollution in sediments of the Pasvik River drainage. Chemosphere. 2001; 42(1):9-18
Chester R, Kudoja WM, Thomas A, Towner J. Pollution reconnaissance in stream sediments using non-residual trace metals. Environmental Pollution. 1985; 10(3):213-238
Paetzel M, Nes G, Leifsen LO, Schrader H. Sediment pollution in the Vagen, Bergen harbour, Norway. Environmental Geology. 2003; 43(4):476-483
Muniz P, Danula E, Yannicelli B, Garcia-Alonso J, Medina G, Bicego MC. Assessment of contamination by heavy metals and petroleum hydrocarbons in sediments of Montevideo Harbour (Uruguay). Environment International. 2004; 29(8):1019-1028
Fatoki OS, Mathabatha S. An assessment of heavy metal pollution in the East London and Port Elizabeth Harbours. Water SA. 2001; 27(2):233-240
McCready S, Birch GF, Long ER. Metallic and organic contaminants in sediments of Sydney Harbour, Australia and Vicinity—A chemical dataset for evaluating sediment quality guidelines. Environment International. 2006; 32(4):455-465
Zhang LP, Ye X, Feng H, Jing YH, Ouyang T, Yu XT, et al. Heavy metal contamination in western Xiamen Bay sediments and its vicinity, China. Marine Pollution Bulletin. 2007; 54(7):974-982
Ankley GT, Lodge K, Call DJ, Balcer MD, Brooke LT, Cook PM, et al. Heavy metal concentration in surface sediments in a nearshore environment, Jurujuba Sound, Southeast Brazil. Environment Pollution. 1992; 109(1):1-9
Leivuori M. Heavy metal contamination in surface sediments in the Gulf of Finland and comparison with the Gulf of Bothnia. Chemosphere. 1998; 36(1):43-59
Gibbs RJ. Water chemistry of the Amazon River. Geochimica et Cosmochimica Acta. 1973; 36(9):1006-1066
Wen X, Allen HE. Mobilization of heavy metals from Le An River sediments. The Science of the Total Environment. 1999; 227(2-3):101-108
Ravichandran M, Baskaran M, Santschi PH, Bianchi TS. History of trace–metal pollution in Sabine-Neches Estuary, Beaumount, Texas. Environmental Science and Technology. 1995; 29(6):1495-1503
Calmano W, Hong J, Forstner U. Binding and mobilization of heavy metals in contaminated sediments affected by pH and redox potential. Water Science and Technology. 1993; 28(8-9):223-235
Daskalakis KD, O’connor TP. Distribution of chemical concentrations in US coastal and estuarine sediment. Marine Environmental Research. 1995; 40(4):381-398
Argese E, Bettiol C. Heavy metal partitioning in sediments from the lagoon of Venice (Italy). Toxicological and Environmental Chemistry. 2001; 79(3-4):157-170
Chapman PM, Wang F. Assessing sediment contamination in estuaries. Environmental Toxicology and Chemistry. 2001; 20(1):3-22
Wan GJ, Bai ZG, Qing H, Mather JD, Huang RG, Wang HR, et al. Geochemical records in recent sediments of Lake Erhai: Implications for environmental changes in low latitude–high altitude lake in Southwest China. Journal of Asian Earth Science. 2001; 21(5):489-502
Song JM. Biogeochemistry of China marginal seas. Shandong Press of Science and Technology. 2004:1-591
Casado-Martinez MC, Buceta JL, Belzunce MJ, DelValls A. Using sediment quality guidelines for dredged material management in commercial ports from Spain. Environment International. 2006; 32(3):388-396
Dai JC, Song JM, Li XG, Yuan HM, Li N, Zheng GX. Environmental changes reflected by sedimentary geochemistry in recent hundred years of Jiaozhou Bay, North China. Environmental Pollution. 2007; 145(3):656-667
Kalis AJ, Merkt J, Wunderlich J. Environmental changes during the Holocene climatic optimum in Central Europe — Human impact and natural causes. Quaternary Science Reviews. 2003; 22(1):33-79
Hamed MA, Emara AM. Marine molluscs as biomonitors for heavy metal levels in the Gulf of Suez, Red Sea. Journal of Marine System. 2006; 60(3-4):220-234
Horowitz AJ, Rinella FA, Lamothe P, Miller TL, Edwars TK, Roche RL, et al. Variation in suspended sediment and associated trace element concentrations in selected riverine cross sections. Environmental Science and Technology. 1990; 24(9):1313-1320
Szefer P, Kusak A, Jankowska H, Wolowicz M, Ali AA. Distribution of selected metals in sediment cores of Puck Bay, Baltic Sea. Marine Pollution Bulletin. 1995; 30(9):615-618
Horowitz AJ, Elrick K. The relation of stream sediments surface area, grain size and composition to trace element chemistry. Applied Geochemistry. 1987; 2(4):437-451
de Groot AJ, Salomons W, Allersma E. Processes affecting heavy metals in estuarine sediments. In: Burton JD, Liss PS, editors. Estuarine Chemistry. London: Academic Press; 1976. pp. 131-157
Pekey H, Karakas D, Bakacoglu M. Source apportionment of trace metals in surface waters of a polluted stream using multivariate statistical analyses. Marine Pollution Bulletin. 2004; 49(9-10):809-818
Ong MC, Fok FM, Sultan K, Joseph B. Distribution of heavy metals and rare earth elements in the surface sediments of Penang River Estuary, Malaysia. Open Journal of Marine Science. 2016; 6(1):79-92
Tam NFY, Wong WS. Spatial variation of heavy metals in surface sediments of Hong Kong mangrove swamps. Environmental Pollution. 2000; 110(2):195-205
Bettinetti R, Giarei C, Provini A. A chemical analysis and sediment toxicity bioassays to assess the contamination of the River Lambro (Northern Italy). Archieves of Environmental Contamination and Toxicology. 2003; 45(1):72-80
Chapman PM. The sediment quality triad: Then, now and tomorrow. International Journal of Environment and Pollution. 2000; 13(1-6):351-360
Livingstone DA, Boykin JC. Vertical distribution of phosphorus in Linsley pond mud. Limnology Oceanography. 1962; 7:57-63
Robbins JA, Edgington DN. Determination of recent sedimentation rates in Lake Michigan using Pb–210 and Cs–137. Geochimica et Cosmochimica Acta. 1975; 39(3):285-304
Abrao JJ, Marques A, Bernat M, Wasserman JC, Lacerda LD. Metal Concentration in 210Pb Dated Sediment Profiles from a Sub-Tropical Brazilian Lagoon. Cartagena: International Symposium on Environmental Geochemistry in Tropical Countries; 1996. pp. 1-5
Rubio B, Nombela MA, Vilas F. Geochemistry of major and trace elements in Ssediments of the Ria de Vigo (NW Spain): An assessment of metal pollution. Marine Pollution Bulletin. 2000; 40(11):968-980
Liu W, Li X, Shen Z, Wang D, Wai O, Li Y. Multivariate statistical study of heavy metal enrichment in sediments of the Pearl River Estuary. Environmental Pollution. 2003; 121(3):377-388
El Nemr A. Assessment of heavy metal pollution in surface muddy sediments of lake Burullus, southeastern Mediterranean, Egypt. Egyptian Journal of Aquatic Biology and Fisheries. 2003; 7(4):67-90
Santos IR, Silva-Filho EV, Schaefer CE, Albuquerque-Filho MR, Campos LS. Heavy metals contamination in coastal sediments and soils near the Brazilian Antarctic Station, King George Island. Marine Pollution Bulletin. 2005; 50(2):185-194
van der Weijden CH. Pitfalls of normalization of marine geochemical data using a common divisor. Marine Geology. 2002; 184(3-4):167-187
Cobelo-García A, Prego R. Heavy metal sedimentary record in a Galician Ria (NW Spain): Background values and recent contamination. Marine Pollution Bulletin. 2003; 46(10):1253-1262
Emmerson RHC, O’Reilly-Wiese SB, Macleod CL, Lester JN. A multivariate assessment of metal distribution in intertidal sediments of the Blackwater Estuary, UK. Marine Pollution Bulletin. 1997; 34(11):484-491
Lee CL, Fang MD, Hsieh MT. Characterization and distribution of metals in surficial sediments in Southwestern Taiwan. Marine Pollution Bulletin. 1998; 36(6):464-471
Loring DH. Lithium—A new approach for the granulometric normalization of trace metal data. Marine Chemistry. 1990; 29:155-168
Aloupi M, Angelidis MO. Normalization to lithium for the assessment of metal contamination in coastal sediment cores from the Aegean Sea, Greece. Marine Environment Research. 2001; 52(1):1-12
Soto-Jiménez MF, Paez-Osuna F. Distribution and normalization of heavy metal concentration in mangrove and lagoon sediments from Mazaltan (Gulf of California) Estuarine. Estuarine Coastal and Shelf Science. 2001; 53(3):259-274
Tuncel SG, Tugrul S, Topal T. A case study on trace metals in surface sediments and dissolved inorganic nutrients in surface water of Ölüdeniz Lagoon–Mediterranean, Turkey. Water Research. 2007; 41(2):365-372
Tessier E, Garnier C, Mullot JU, Lenoble V, Arnaud M, Raynaud M, et al. Study of the spatial and historical distribution of sediment inorganic contamination in the Toulon bay (France). Marine Pollution Bulletin. 2011; 62(10):2075-2086
Grousset FE, Quetel CR, Thomas B, Donard OFX, Lambert CE, Quillard F, et al. Anthropogenic vs lithogenic origins of trace element (As, Cd, Pb, Rb, Sb, Sc, Sn, Zn) in water column particles: Northwestern Mediterranean Sea. Marine Chemistry. 1995; 48(3-4):291-310
Ackerman F. A procedure for correcting grain size effect in heavy metal analysis of estuarine and coastal sediments. Environment Technology Letters. 1980; 1(11):518-527
Roussiez V, Ludwig W, Probst JL, Monaco A. Background levels of heavy metals in surficial sediments of the Gulf of Lions (NW Mediterranean): An approach based on 133Cs normalization and lead isotope measurements. Environmental Pollution. 2005; 138(1):167-177
Matthai C, Birch G. Detection of anthropogenic Cu, Pb and Zn in continental shelf sediments off Sydney, Australia—A new approach using normalization with cobalt. Marine Pollution Bulletin. 2001; 42(11):1055-1063
Larrose A, Coynel A, Schäfer J, Blanc G, Massé L, Maneux E. Assessing the current state of the Gironde estuary by mapping priority contaminant distribution and risk potential in surface sediment. Applied Geochemistry. 2010; 25(12):1912-1923
Strady E, Kervella S, Blanc G, Robert S, Stanisière JY, Coynel A, et al. Spatial and temporal variations in trace metal concentrations in surface sediments of the Marenne Oléron bay. Relation to hydrodynamic forcing. Continental Shelf Research. 2011; 31(9):997-1007
Din ZB. Use of aluminium to normalize heavy metal data from estuarine and coastal sediments of straits of Melaka. Marine Pollution Bulletin. 1992; 24(10):484-491
Tam NFY, Yao MWY. Normalization and heavy metal contamination in mangrove sediments. The Science of the Total Environment. 1998; 216(1-2):33-39
Schiff KC, Weisberg SB. Iron as a reference element for determining trace metal enrichment in Southern California coast shelf sediments. Marine Environmental Research. 1999; 48(2):161-176
Rubio B, Nombela MA, Vilas F. Geochemistry of major and trace elements in sediments of the Ria de Vigo (NW Spain): An assessment of metal pollution. Marine Pollution Bulletin. 2000; 40(11):968-980
Cobelo-García A, Prego R. Influence of point sources on trace metal contamination and distribution in a semi-enclosed industrial embayment: The Ferrol Ria (NW Spain). Estuarine, Coastal and Shelf Science. 2004; 60(4):695-703
Jiang FQ , Li AC. Geochemical characteristics and their implications to provenance and environment of surface sediments from the South Okinawa Trough. Acta Sedimentologic Sinica. 2002; 20(4):680-686
Zhang J, Liu CL. Riverine composition and estuarine geochemistry of particulate metals in China weathering features, anthropogenic impact and chemical fluxes. Estuarine, Coastal and Shelf Science. 2002; 54(6):1051-1070
Feng X, Li G, Qiu G. A preliminary study on mercury contamination to the environment from artisanal zinc smelting using indigenous methods in Hezhang country, Guizhou, China–Part 1: Mercury emission from zinc smelting and its influences on the surface waters. Atmospheric Environment. 2004; 38(36):6223-6230
Muller G. Index of geoaccumulation in sediments of the Rhine River. Geology Journal. 1969; 2(3):109-118
Wedepohl KH. The composition of the continental crust. Geochimica et Cosmochimica Acta. 1995; 59(7):1217-1232
Tomlinson DL, Wilson CR, Harris CR, Jeffrey DW. Problems in the assessment of heavy-metal levels in the estuaries and the formation of a pollution index. Hergoland Marine Research. 1980; 33(1-4):566-575
Karbassi AR, Bayati I, Moatta F. Origin and chemical partitioning of heavy metals in riverbed sediments. International Journal of Environmental Science and Technology. 2006; 3(1):35-42
Priju CP, Narayana AC. Heavy and trace metals in Vembanad lake sediments. International Journal of Environmental Research. 2007; 1(4):280-289
Rabee AM, Al-Fatlawy YF, Najim AA, Nameer M. Using pollution load index (PLI) and geoaccumulation index (I–geo) for the assessment of heavy metals pollution in Tigris river sediment in Baghdad region. Journal of Al-Nahrain University. 2011; 14(4):108-114
Harikumar PS, Jisha TS. Distribution pattern of trace metal pollutants in the sediments of an urban wetland in the southwest coast of India. International Journal of Engineering Science and Technology. 2019; 2(5):840-850
Chakravarty M, Patgiri AD. Metal pollution assessment in sediments of the Dikrong River, NE India. Journal of Human Ecology. 2009; 27(1):63-67
Seshan BRR, Natesan U, Deepthi K.Geochemical and statistical approach for evaluation of heavy metal pollution in core sediments in southeast coast of India. International Journal of Environmental Science and Technology. 2010; 7(2):291-306
Long ER, MacDonald DD, Smith SL, Calder FD. Incidence of adverse biological effects within range of chemical concentrations in marine and estuarine sediments. Environmental Management. 1995; 19(1):18-97
Smith SL, MacDonald DD, Keenleyside KA, Ingersoll CG, Field J. A preliminary evaluation of sediment quality assessment values for freshwater ecosystems. Journal of Great Lakes Research. 1996; 22(3):624-638
Schaffner M, Bader HP, Scheidegger R. Modeling the contribution of point sources and non-point sources to Thachin River water pollution. Science of the Total Environment. 2009; 407(17):4902-4915
O’Regan PR. The use of contemporary information technologies for coastal research and management—A review. Journal of Coastal Research. 1996; 12(1):192-204
Zhou F, Guo HC, Hao ZJ. Spatial distribution of heavy metals in Hong Kong’s marine sediments and their human impacts: A GIS-based chemometric approach. Marine Pollution Bulletin. 2007; 54(9):1372-1384
Davis HT, Aelion CM, McDermott S, Lawson AB. Identifying natural and anthropogenic sources of metals in urban and rural soils using GIS-based data, PCA, and spatial interpolation. Environmental Pollution. 2009; 157(8-9):2378-2385
Zhou F, Guo HC, Liu L. Quantitative identification and source apportionment of anthropogenic heavy metals in marine sediment of Hong Kong. Environmental Geology. 2007; 53(2):295-305
Poggio L, Borut V, Schulin R, Hepperle E, Marsan FA. Metals pollution and human bioaccessibility of topsoils in Grugliasco (Italy). Environmental Pollution. 2009; 157(2):680-689
Langran G. A review of temporal database research and its use in GIS applications. International Journal of Geographical Information System. 1989; 3(3):215-232
Carrara A, Cardinali M, Detti R, Guzzeti F, Pasqui V, Reichenbach P. GIS techniques and statistical models in evaluating landslide hazard. Earth Surface Processess Landforms. 1991; 16(5):427-445
Facchinelli A, Sacchi E, Mallen L. Multivariate statistical and GIS-based approach to identify heavy metal sources in soils. Environmental Pollution. 2001; 114(3):313-324
Yin K, Lin ZF, Ke ZY. Temporal and spatial distribution of dissolved oxygen in the Pearl River Estuary and adjacent coastal waters. Continental Shelf Research. 2004; 24(16):1935-1948
Lee CSL, Li XD, Shi WZ, Cheung SCN, Thornton I. Metal contamination in urban, suburban and country park soils of Hong Kong: A study based on GIS and multivariate statistics. The Science of the Total Environment. 2006; 356(1-3):45-61
Chowdary VM, Rao NH, Sarma PBS. Decision support framework for assessment of non-point-source pollution of groundwater in large irrigation projects. Agricultural Water Management. 2005; 75(3):194-225
Labonne M, Othman DB, Luck JM. Pb isotopes in mussels as tracers of metal sources and water movements in a lagoon (Thau Basin, S. France). Chemical Geology. 2001; 181(1):181-191
Goodwin TH, Young AR, Holmes MGR, Old GH, Hewitt N, Leeks GJL, et al. The temporal and spatial variability of sediment transport and yields within the Bradford Beck catchment, West Yorkshire. Science of the Total Environment. 2003; 314-316:475-494
Gelinas Y, Schmit JP. Extending the use of the stable lead isotope ratios as a tracer in bioavailability studies. Environmental Science and Technology. 1997; 31(7):1968-1972
Ip CCM, Li XD, Zhang G, Wong CSC, Zhang WL. Heavy metal and Pb isotopic compositions of aquatic organisms in the Pearl River Estuary, South China. Environmental Pollution. 2005; 138(3):495-505
Ong MC, Kamaruzaman MI, Yong JC, Kamaruzzaman BY, Joseph B. Metals contamination using Polymesoda expansa(Marsh Clam) as bio–indicator in Kelantan River, Malaysia. Malaysian Journal of Analytical Sciences. 2017; 21(3):597-604
Ong MC, Amalina I. Determination of selected metallic element in marsh clam, Polymesoda expansa, collected from Tanjung Lumpur mangrove forest, Kuantan, Pahang. Borneo Journal of Marine Science & Aquaculture. 2017; 1(1):65-70
Phillips DJH. Arsenic in aquatic organisms: A review emphasising chemical speciation. Aquatic Toxicology. 1990; 16(3):151-186
Rainbow PS. Trace metal accumulation in marine invertebrates: Marine biology or marine chemistry? Journal of the Marine Biological Association of the United Kingdom. 1997; 77:195-210
Ong MC, Kamaruzaman MI, Siti Noorhidayah A, Joseph B. Trace metals in highly commercial fishes caught along coastal water of Setiu, Terengganu, Malaysia. International Journal of Applied Chemistry. 2016; 12(4):773-784
Ong MC, Gan SL. Assessment of metallic trace elements in the muscles and fins of four landed elasmobranchs from Kuala Terengganu waters, Malaysia. Marine Pollution Bulletin. 2017; 124(2):1001-1005
Blais JM, Macdonald RW, Mackay D, Webster E, Harvey C, Smol JP. Biological mediated transport of contaminants to aquatic systems. Environmental Science and Technology. 2007; 41(4):1075-1084
Erickson RJ, Nichols JW, Cook PM, Ankley GT. Chapter 2. Bioavailability of chemical contaminants in aquatic systems. The Toxicology of Fishes. 2008:9-54
Liu JK, He X. Quatitative and qualitative aspects of fish corp in relation to environmental quality. Ecotoxicology and Environmental Safety. 1987; 13(1):61-75
Anderson RS. Lack of hemocyte chemiluminescence stimulation by Perkinsus marinus in eastern oysters Crassostrea irginica with dermo disease. Journal of Aquatic Animal Health. 1999; 11(2):179-182
Bryan GW, Langston WJ, Hummerstone LG, Burt GR. A Guide to the Assessment of Heavy Metal Contamination in Estuaries Using Biological Indicators. Plymouth: Occasional Publication of the Marine Biological Association 4, Marine Biology of the United Kingdom; 1985. 92 p
Rainbow PS. Biomonitoring of heavy metal availability in the marine environment. Marine Pollution Bulletin. 1995; 31(4-12):183-192
Bryan GW, Langston WJ, Hummerstone LG. The use of biological indicators of heavy metal contamination in estuaries: With special reference to an assessment of the biological availability of metals in estuarine sediments from south-west Britain. Marine Biological Association of the United Kingdom. 1980; 1:73
Butler PA, Andren L, Bonde GJ, Jernelov A, Reisch DJ. Monitoring organisms. In: Ruivo M, editor. Food and Agricultural Organisation Technical Conference on Marine Pollution and its Effects on Living Resources and Fishing, Rome, 1970. Supplement 1: Methods of Detection, Measurement and Monitoring of Pollutants in the Marine Environment. London: Fishing News Books; 1971. pp. 101-112