characterization of accumulated sediments in bio-remediation chamber at estero de balete

CHEMICAL ENGINEERING

ADAMSON UNIVERSITY

CHARACTERIZATION OF ACCUMULATED

SEDIMENTS IN BIO-REMEDIATION

CHAMBERS AT ESTERO DE BALETE

Banta, Mhadel A.

Candelaria, Camille G.

Pagasartonga, Mon Eric P.

Ricarte, Shienah C.


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Adamson University

College of Engineering

Chemical Engineering Department

A Research Study Presented to

The Faculty of Chemical Engineering Department

In Partial Fulfillment of the

Requirements for the Degree of

Bachelor of Science in Chemical Engineering

CHARACTERIZATION OF ACCUMULATED SEDIMENTS IN

BIO-REMEDIATION CHAMBERS AT ESTERO DE BALETE

Banta, Mhadel A.

Candelaria, Camille G.

Pagasartonga, Mon Eric P.

Ricarte, Shienah C.

APRIL 2011


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APPROVAL SHEET

This research entitled:

“Characterization of Accumulated Sediments in Bio-Remediation Chambers at

Estero De Balete”

Prepared and submitted by:

Banta, Mhadel A. Candelaria, Camille G,

Pagasartonga, Mon Eric P. Ricarte, Shienah C.

Engr. Jerry G. Olay

Adviser

Has been successfully defended last March 29, 2011 and was approved last April 12,

2011.

Engr. Sherrie Mae S. Medez

Panelist

Engr. Merlinda A. Palencia

Chairperson


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DECLARATION

This research study hereto is entitled:

“Characterization of Accumulated Sediments in Bio-Remediation Chambers at

Estero De Balete”

This report is a summary of our findings from the work we completed this 2nd

semester

of 2011 and is submitted as an output for compliance with the requirements leading to

the Degree of Bachelor of Science in Chemical Engineering.

Prepared and submitted by:

Banta, Mhadel A. Candelaria, Camille G,

Pagasartonga, Mon Eric P. Ricarte, Shienah C.

Engr. Merlinda Palencia

Chairperson


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ACKNOWLEDGEMENT

We would like to dedicate this study first of all to God Almighty, He who

helped and guided us all throughout our experiment.

We would like also to take the opportunity to acknowledge Engr. Palencia for

allowing us to be part of her study. It is our honor to take part in behalf of Adamson

University ChE Student Research for the rehabilitation of Estero De Balete. Our

adviser, Engr. Olay, for giving us his time unconditionally. Engr. Evangelista, for

being patient with us at the ChE Laboratory.

Allow us also to give token of appreciation to our fellow classmates by citing

them here. We thank all of you classmates, batch mates and friends. We also

acknowledge our family by supporting us regardless our misgiving.

In behalf of our Research Group, we hope that this study can be a reliable

guide in rehabilitating the Estero de Balete.


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Table of Contents

Abstract i

List of Figures and Tables iii

1 Introduction 1

1.1 Background of Study 1

1.2 Statement of the Study 2

1.3 Significance of the Study 3

1.4 Scope and Delimitation of the Study 3

1.5 Theoretical Framework 4

1.6 Conceptual Framework 6

1.7 Definition of Terms 7

2 Review of Related Literature and Studies 9

2.1 Related Literature 9

2.1.1 Sediments 9

2.1.2 Effects of Heavy Metal Contamination in Human Health and the

Environment 11

2.1.3 Sediments Quality Guidelines 15

2.1.4 Bioremediation 20

2.1.5 Total Organic Carbon 21

2.1.6 Total Phosphorus 22

2.1.7 Total Kjeldahl Nitrogen 24

2.1.8 Equipment 25

2.2 Related Studies 26

3 Methodology 31

3.1 Description of Study Area 31

3.2 Preparation of Sampling Bed and Containers 32

3.3 Selection of Sampling Site 33

3.4 Collection of Sediment Samples 33


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4 Data Presentation, Analysis and Interpretation of Results 35

4.1 Physical Properties of Collected Sediments 35

4.2 Heavy Metal Concentration of Collected Sediments 36

4.3 Nutrient Content of Collected Sediments 37

4.4 Assessment of Collected Sediments using Sediment Quality

Guidelines 38

4.4.1 Ontario Ministry Sediment Quality Guideline 38

4.4.2 Hong Kong Sediment Quality Guideline 44

4.5 Accumulation Rate of Sediments 47

5 Summary of Findings, Conclusions and Recommendations 48

5.1 Summary of Findings 48

5.2 Conclusions 49

5.3 Recommendations 50

Appendices 51

Appendix A: Results of Analyses 51

Appendix B: Calculation of Accumulation Rate of Sediments 53

Appendix C: Research Images 55

Appendix D: References 60

Resume of Researchers 63


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Abstract

Estero de Balete is one of the tributaries of Pasig River that have been

contaminated because of accumulation of wastes and refuse which are hazardous in

nature. In this study, a Bioremediation test was done on Estero de Balete and the

physical and chemical properties of accumulated sediments were determined. Also,

determination of heavy metal content (Copper, Lead, Cadmium and Mercury) of

sediments was also part of this study.

The remediation technique was conducted for about 2 months. Two runs were

done but the analysis for the second run was used in this report because more

significant change in the contaminants was observed. The concentrations of the heavy

metals were measured using Flame Atomic Absorption Spectrophotometer (AAS)

while the nutrient contents (Total Kjeldahl Nitrogen, Total Phosphorus and Total

Organic Carbon) of sediments were determined using Kjeldahl Method, Stannous

Chloride Method and Ascorbic Acid Method.

In the Philippines, there are currently no Sediment Quality standards and the

most commonly used guidelines are from Ontario Sediment Quality Guidelines and

National Oceanic Atmospheric Administration (NOAA). For this study, we have

compared the attained sediment analysis with Ontario Sediment Quality Guidelines

and Hong Kong Sediment Quality Guidelines to determine if the collected sediments

would have any adverse effect to the environment. Results showed that, after the

remediation, the contaminants pose no serious effect to the environment.

The analysis in this study could be of great help in finding ways to decrease the

contamination of these hazardous substances in Rivers and in its tributaries that induce

harmful effects to the environment and human help. This study can also be used as

technical references in the rehabilitation of Pasig River.


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List of Figures and Tables

Figure 1 Experimental Procedure

Figure 3.1a Bioremediation Chambers

Figure 3.1b Experimental Design for the Determination of Accumulation Rate

Figure 3.2 Sampling Bed

Figure 3.3 Sampling Points for Determination of Accumulation Rate

Figure 4.2 Graphical Representation of Heavy Metal Concentrations of Collected

Sediments

Figure 4.3 Graphical Representation of Nutrient Concentrations of Collected

Sediments

Figure 4.4a Comparison of Copper Concentration from the Collected Sediments with

Ontario Sediment Quality Guidelines

Figure 4.4b Comparison of Lead Concentration from the Collected Sediments with

Ontario Sediment Quality Guidelines

Figure 4.4c Comparison of Cadmium Concentration from the Collected Sediments

with Ontario Sediment Quality Guidelines

Figure 4.4d Comparison of Mercury Concentration from the Collected Sediments

with Ontario Sediment Quality Guidelines

Figure 4.4e Comparison of Total Kjeldahl Nitrogen Concentration from the

Collected Sediments with Ontario Sediment Quality Guidelines

Figure 4.4f Comparison of Total Phosphorus Concentration from the Collected

Sediments with Ontario Sediment Quality Guidelines

Figure 4.4g Comparison of Total Organic Carbon Concentration from the Collected


Figure 4.4h Comparison of Copper Concentration from the Collected Sediments with

Hong Kong Sediment Quality Guideline

Figure 4.4i Comparison of Lead Concentration from the Collected Sediments with

Hong Kong Sediment Quality Guideline


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Figure 4.4j Comparison of Mercury Concentration from the Collected Sediments

with Hong Kong Sediment Quality Guideline

Table 2.1 Ontario Ministry of Screening Level Guidelines

Table 3.4 Methods Used for the Analysis of Total Phosphorus, Total Organic

Carbon, Total Nitrogen and Heavy Metals

Table 4.1 Physical Properties of Collected Sediments

Table 2.2 Ontario Sediment Quality Benchmarks

Table 2.3 Sediment quality guideline values Lower Concentration Exceedance

Level (LCEL) and Upper Concentration Exceedance Level (UCEL) of

Hong Kong

Table 4.5 Accumulation Rate of Sediments in each Filter Bed per Unit Area

Table 5.1 Concentrations of Lead, Mercury, Copper, Cadmium and Nutrients from

Sediments Collected after the Bioremediation Treatment and from Sediment Quality

Guidelines (ppm)


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CHAPTER 1

INTRODUCTION

1.1 Background of Study

Sediments are loose particles of clay, silt and other substances that settle at the

bottom of water body. Sediments play an important role in aquatic ecosystem since

they serve as a source and sink for organic and inorganic materials and as habitat for

many organisms in aquatic food webs. The series of sediment-induced changes that

can occur in a water body may change the composition of an aquatic community

(Wilber, 1983). Nowadays, many of these sediments in our lakes, rivers, oceans and

other bodies of water have been contaminated by pollutants, which enter our bodies of

water. Experts believed that contaminated sediments are a wide spread and serious

problem. Recent studies revealed that the true state of the quality of water is reflected

by the quality of its underlying sediments.

The Pasig River one of the major Rivers in the Philippines serves as a major

transport route, source of water and life line of Laguna de Bay and irreplaceable

natural resources. Yet, for centuries Pasig River has been used, abused and neglected

and not the River has been declares a critical water body because of the unspeakable

amount of waste dumped into it by daily household and industries. About 330 tons of

industrial and domestic wastes are discharge every day in this water way, depleting the

biochemical oxygen needed to support marine life. (Menchit R. Santelices)

Until recently, little has been done to protect the river system. Past efforts to

rehabilitate Pasig River were unsuccessful because they failed to take into account the

larger context of the urban environment of which Pasig River is apart.

Recently, Adamson University, together with Chemical Engineering

department, established “Bio-remediation Techniques for Rehabilitation of Estero de


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Balete” which aims to revive and rehabilitate the water and sediments of Estero de

Balete through the application of natural minerals available in the Philippines. The

information on the effects of locally available natural materials on the treatment of

Estero water and sediments will provide concrete technical and methodical basis to

rehabilitate Pasig River into a more stable ecosystem.

1.2 Statement of the Study

This study aims to determine the characteristic of sediments that settled from

the treated water in the bioremediation chambers at Estero de Balete. Specifically, the

study aims to:

1. Determine the physical and chemical characteristic of the sediments of

Estero de Balete in terms of the following parameters:

1.1 Physical properties

1.1.1 Color

1.1.2 Odor

1.2 Chemical properties

1.2.1 Total Phosphorus

1.2.2 Total Kjeldahl Nitrogen

1.2.3 Total Organic Carbon

2. Measure the concentration of cadmium, copper, mercury and lead the

sediments

3. Evaluate the extent of heavy metal and nutrients, i.e. Total Phosphorus,

Total Kjeldahl Nitrogen and Total Organic Carbon, of sediments in terms

of the following guidelines:

3.1 Ontario Sediment Quality Guidelines

3.2 Hong Kong Sediment Quality Guideline

4. Determine the daily sludge formation/ accumulation rate


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1.3 Significance of the Study

The physical and chemical characterizations of accumulated sediments in

bioremediation chamber are the primary concern of the study. Through this research,

the Adamson community and people living along the Estero would be aware of the

possible problem regarding contamination of sediments, this enable us to focus our

efforts on activities that achieve the best environmental results. Finally, the

characteristic of sediments gathered may help establish an effective bioremediation

treatment for Estero de Balete.

1.4 Scope and Delimitation of the Study

The study focused on the characterization of the physical and chemical

properties of sediments on the bioremediation chamber at Estero de Balete.

Sediment sampling was done only after the removal of treated water in the

chamber. There are two chambers and only three sites of the chamber are to be

considered. The heavy metals determined were cadmium (Cd), copper (Cu), mercury

(Hg) and lead (Pb).The comparison of the level of heavy metal contamination of

sediments with environmental protection agency (EPA) level of hazardous chemicals

focused on the four metals mention above and also comparing the results with the

established heavy metal concentration of sediments found in Estero de Balete.

Determination of total nitrogen and phosphorus and total organic carbon is also

considered. Biological characteristic of sediments such as soil form organism, specific

microorganism and total toxicity are not assessed. Under the physical characteristics of

sediments the following are determined: color and odor. The study will also determine

the daily sludge formation or accumulation rate per unit area.


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1.5 Theoretical Framework

Many of the sediments in our rivers, lakes, and oceans have been contaminated

by pollutants. Some of these pollutants, such as the pesticide and the industrial

chemicals, were released into the environment long ago. Other contaminants enter our

waters every day. Some flow directly from industrial and municipal waste dischargers,

while others come from polluted runoff in urban and agricultural areas. Still other

contaminants are carried through the air, landing in lakes and streams far from the

factories and other facilities that produced them.

Heavy metals are one of the most persistent pollutants in water. Unlike other

pollutants, they are difficult to degrade, but can accumulate throughout the food chain,

producing potential human health risks and ecological disturbances. Their presence in

water is due to discharges from residential dwellings, groundwater infiltration and

industrial discharges. The discharge of wastewater containing high concentrations of

heavy metals to receiving water bodies has serious adverse environmental effects.

Their occurrence and accumulation in the environment is a result of direct or indirect

human activities, such as rapid industrialization, urbanization and anthropogenic

sources (EPA, 2000; Hussein et al., 2005; Gardea-Torresdey et al., 2005; Martin-

Gonzalez et al., 2006).

A small amount of contamination of heavy metal to our bodies of water may

lead to serious environmental problem. Heavy metals can either be absorbed by the

sediments or accumulated by benthic organism to toxic levels; the bioavailability and

subsequent toxicity of the metals are dependent upon the various forms and amount of

the metal bound to the sediments.

Sediment quality is determined according to its effect on water quality and

aquatic life. The No Effect Level (NEL) has zero effect on the aquatic living

organisms. The Low Effect Level (LEL) is the Level in which there is little effect on


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the sediment–dwelling organisms. At the Severe Effect Level (SEL) affects the health

of the sediment-dwelling organisms and is considered to be heavily polluted.

Also, sediment quality is also determined based on its level of toxicity. The

lower chemical exceedance level (LCEL) represents a value below which

contaminants in the sediment are not expected to have adverse biological effects,

whereas the upper chemical exceedance level (UCEL) represents a value above which

toxicity is likely.


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1.6 Conceptual Framework

Figure 1 Experimental Procedure

Collection of

samples

Preparation of

containers

Laboratory analysis

Heavy Metal

Analysis

(Cd, Cu, Hg and Pb)

Physical

Properties

Chemical

Properties

Color

Odor

Total

Phosphorus

Content

Total Organic

Carbon Content

Interpretation of

Data

Drawing of

Conclusion

Total Nitrogen

Content

Preparation of

sampling bed

Collection of

samples

Accumulation Rate

Determination


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1.7 Definition of Terms

1. Bioavailability- the rate at which a substance is absorbed or becomes

available at site.

2. Bioremediation Chambers - chambers at which the water treatment is done.

These are located within Estero de Balete.

3. Heavy metal - refers to any metallic chemical element that has a relatively

high density and is toxic or poisonous at low concentrations. Examples of

heavy metals include mercury (Hg), cadmium (Cd), arsenic (As), chromium

(Cr), thallium (Tl), and lead (Pb).

4. Odor - is caused by one or more volatilized chemical compounds, generally at

a very low concentration, that humans or other animals perceive by thesense

of olfaction.

5. Oxygen-Releasing Compound (ORC or biominerals) – is the medium used

in water treatment which is designed specifically to release oxygen, in a

controlled fashion, into groundwater to stimulate cost effective in situ

bioremediation of contaminants. In this study, the ORC used is a calcium-

based compound.

6. Powder Dispersion Method - is a method of water treatment wherein the

ORC are being dispersed evenly within the bioremediation chamber

7. Sediment - is naturally-occurring material that is broken down by processes

of weathering and erosion, and is subsequently transported by the action of

fluids such as wind, water, or ice, and/or by the force of gravity acting on the

http://www.lenntech.com/Periodic-chart-elements/Hg-en.htm

http://www.lenntech.com/Periodic-chart-elements/Cd-en.htm

http://www.lenntech.com/Periodic-chart-elements/As-en.htm

http://www.lenntech.com/Periodic-chart-elements/Cr-en.htm

http://www.lenntech.com/Periodic-chart-elements/Tl-en.htm

http://www.lenntech.com/Periodic-chart-elements/Pb-en.htm


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particle itself. Sediments are most often transported by water (fluvial

processes) transported by wind (Aeolian) and glaciers. Beach sands and river

to channel deposits are examples of fluvial transport and deposition, though

sediment also often settles out of slow-moving or standing water in lakes and

oceans. Deserts and loess are examples of Aeolian transport and deposition.

Glacial moraine deposits and till are ice transported sediments.

8. Tea Bag Method - is a method of water treatment wherein the ORC is placed

in tea bags. These tea bags are distributed evenly within the bioremediation

chamber. These bags are suspended and must be of about 3-4 inches above the

chamber floor. This method is done after the Powder Dispersion Method.

9. Total Kjeldahl Nitrogen content - refers to the measure of all forms of

nitrogen (organic and inorganic). Nitrogen is an essential plant element and is

often the limiting nutrient in marine waters

10. Total Organic Carbon (TOC) - is the amount of carbon bound in an organic

compound and is often used as a non-specific indicator of water quality or

cleanliness of pharmaceutical manufacturing equipment.

11. Total Phosphorus content- is a measure of both inorganic and organic forms

of phosphorus. Phosphorus can be present as dissolved or particulate matter. It

is an essential plant nutrient and is often the most limiting nutrient to plant

growth in fresh water. It is rarely found in significant concentrations in

surface waters. It is generally reported in µg/l or mg/l. The total phosphorus

concentration in most lakes not affected by anthropogenic inputs is generally

less than 0.01 mg/l (10 µg/l).


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CHAPTER 2

REVIEW OF RELATED LITERATURE AND STUDIES

2.1 Related Literature

2.1.1 Sediments

Many of the sediments in our rivers, lakes, and oceans have been

contaminated by pollutants. Many of the contaminants were released years ago

while other contaminants enter our water every day. Some contaminants flow

directly from industrial and municipal waste dischargers, while others come from

polluted runoff in urban and agricultural areas. Still other contaminants are carried

through the air, landing in lakes and streams far from the factories and other

facilities that produced them (EPA, 1996).

Sediment is any particulate matter that can be transported by fluid flow and

which eventually is deposited as a layer of solid particles on the bed or bottom of a

body of water or other liquid. Sedimentation is the deposition by settling of a

suspended material.

Sedimentation is the tendency for particles in suspension to settle out of the

fluid in which they are entrained, and come to rest against a barrier. This is due to

their motion through the fluid in response to the forces acting on them: these forces

can be due to gravity, centrifugal acceleration or electromagnetism. In geology

sedimentation is often used as the polar opposite of erosion, i.e., the terminal end

of sediment transport. In that sense it includes the termination of transport by

saltation or true bed load transport. Settling is the falling of suspended particles

through the liquid, whereas sedimentation is the termination of the settling process.


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Sediments can become contaminated in a number of ways. Urban runoff

that discharges to surface waters often contains polycyclic aromatic hydrocarbons

(PAHs), oil and grease, and heavy metals. Agricultural runoff may contain

nutrients and pesticides. Industrial spills and releases, especially those that

occurred before controls were in place, can put product into the water. Chemicals

that are denser than water, suchas polychlorinated biphenyls (PCBs) and some

pesticides like DDT, will sink to the bottom of water bodies and directly

contaminate sediments. Atmospheric deposition of substances such as mercury is

another source of sediment contamination as is the discharge of contaminated

groundwater through the sediments to the overlying surface water (USEPA 1999

and USEPA 2005).

Categories of Sediments

Sediments can be divided into three categories; framework bed load, matrix

bed load and suspended bed load.

Framework bed load creates the structure of the bed. They are large

particles that are moved only during large flow events.

The matrix bed load refers to the part of the bed material that is small

enough to be frequently entrained by low to moderate flow but is large enough to

settle out of the water column in lower velocities. They incorporate the sand and

the silt size material.

The suspended bed load is the smallest size class of the total sediments of

the fluvial system (RCA III 1995).


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Sources of Sediments and Sediment Contaminants

Aquatic sediments are principally derived from weathering processes, with

major transportation from terrestrial sources under high runoff from storms and

floods. In addition, discharges from urban, industrial and mining activities are

potential sources of particulates. Anthropogenic contaminants, including metals,

organics and nutrient elements are associated with particulate and dissolved inputs

to natural waters. It is important to distinguish between point source and diffuse

inputs. (Australian and New Zealand Guidelines for Fresh and Marine Water

Quality Volume 2, 2000)

A point source is an input that enters a body of water at a definitive

location and can usually be quantified. Factories (industrial) and municipal

wastewater outfalls are examples of point source discharges. Wastewater sources

may include domestic wastewater infiltration and inflow, and wastewater from

commercial sources such as canneries, agricultural operations, etc. Non-point or

diffuse sources, on the other hand, are discharges that cannot be identified as

coming from one definitive location or point. The discharge often enters the

waterways through overland runoff, through a large number of smaller drainage

pipes, or by precipitation travelling through the surface of the land and water.

2.1.2 Effects of Heavy Metal Contamination in Human Health and the

Environment

Contaminated sediments may be directly toxic to aquatic life or can be a

source of contaminants for bioaccumulation in the food chain. A wide range of


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physical, chemical, and biological factors have the potential to influence the

bioavailability of sediment contaminants (EPA 2004).

Sediment load values are of great ecological importance for an aquatic

system, as they influence turbidity, nutrient concentrations, the absorption of toxic

substances, and bed form characteristics.

Cadmium (Cd)

Cadmium in nature commonly occurs as a sulphide ore, usually found in

association with zinc ores such as sphalerite (CCREM 1987). Cadmium is

economically recoverable only when it occurs in association with zinc-, lead- and

copper-bearing. The principal use of cadmium is as an alloy in electroplating, in

nickel-cadmium batteries, solders, electronic equipment, photography supplies,

glass, ceramics, and plastics (CCREM 1987).

The major anthropogenic sources to the aquatic environment are through

emissions to air and water from mining and smelting and in the manufacture of the

products noted above. Additional losses occur from agricultural uses and from the

burning of fossil fuels (CCREM 1987).

In water, cadmium generally occurs in the Cd(II) form as a constituent of

inorganic (halides, sulphides, oxides) and organic compounds (CCREM 1987).

Cadmium in the water column can exist as free ions (small amount) or complexed

to various ligands such as humic acids, organic particles and various oxides.

Transport of cadmium to the sediments occurs mainly through sorption to organic

matter and subsequent settling, and through coprecipitation with iron, aluminum,

and manganese oxides. Cadmium can also be deposited in sediments through ion

exchange (mainly with calcium) on minerals. These phases account for most of the


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sediment-bound cadmium. Cadmium can also exist in sediments as free ions in the

sediment pore water, as well as bound to other sediment fractions. Sediment pore

water concentrations seem to be controlled by the solubility of iron and manganese

oxyhydroxides in the oxidized layer (particularly as these dissolve under the

advent of reducing conditions) and metal sulphides in the sulphide layer (Moore et

al 1988).

Copper (Cu)

Copper occurs naturally in rocks and minerals either as native copper, or,

more commonly, as a mineral ore. More than 160 copper containing minerals have

been described (CCREM 1987). Since copper is a common element in rock,

weathering of rock can release significant amounts to water. The uses of copper are

highly varied, but principal uses are in alloys, electroplating, electrical wiring,

paints, and pesticides. Copper in aquatic systems can exist in four oxidation states,

of which Cu (I) and Cu (ll) are the most common. Cu (I) under aerobic conditions

is readily oxidized to Cu (II). In natural waters copper undergoes complex

reactions and can be present in solution, either as cupric ions or complexed with

inorganic or organic ligands. Copper is transported to the sediments most often in

association with organic matter, and as precipitates of hydroxides, phosphates and

sulphides. Copper in sediments has a high affinity for hydrous iron and manganese

oxides, clays, carbonate materials and organic matter, though the formation of

these complexes is pH and redox dependent. Under normal pH and inorganic

carbon, most of the copper appears to be present in the form of organic complexes,

cupric carbonate complexes and coprecipitation with iron and manganese oxides

(Brook & Moore 1988; CCREM 1987).

Copper in reducing sediments is primarily in the form of sulphide

complexes, while in the oxidized zone it is mainly present as organic complexes or


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bound to hydrous iron and manganese oxides. Therefore, under anaerobic

conditions, Cu is generally immobilized in the sediments. Release of copper from

sediments can be either through ion exchange, solubilization of the matrix (e.g.

flux of Fe/Mn oxides under reducing conditions) or decomposition of the matrix

(i.e. organic matter). Since copper is an essential micronutrient, it is readily

accumulated by aquatic organisms, especially the lower animals, but no evidence

exists for bio magnification. Some evidence exists to suggest that some organisms

can limit the uptake of copper generally through increases in depuration rates

(Luoma 1983).

Lead (Pb)

Lead occurs naturally as a constituent in a variety of minerals. The single

largest use of lead is in the production of lead-acid batteries, and secondarily, in

the production of chemical compounds such as tetraethyl leads. Other uses include

ammunition manufacturer, paints, glassware, electroplating, electronic equipment,

plastics, solder, specialized containers and construction materials. Weathering of

lead minerals is the principal natural source of lead to the environment.

Anthropogenic sources include street runoff, mining and smelting operations, and

sewage treatment plants. Three oxidation states are of particular environmental

importance in aquatic systems, though of these, Pb (II) is the most stable ionic

species. Transport of lead to sediments is mainly through coprecipitation with

hydrous iron and manganese oxides, complexation with clays (which can also

contain appreciable amounts of iron and manganese hydroxides) and sorption to

organic matter. In sediments, much of the lead is found in association with the

Fe/Mn hydroxides. In oxidized sediments lead is strongly bound to the hydroxide

and organic matter fractions of the sediments. Under reducing conditions lead can

be released to the water column or can form sulphides as the Fe and Mn oxides

dissolve.


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Lead can be bioaccumulated by aquatic organisms. Organisms held at

lower pH (approx. 6.0) accumulated more lead than at higher pH presumably due

to the greater availability of divalent lead at these pH levels. Pb (n) appears to be

the most bioavailable species. In general, the organic forms (e.g. tetraethyllead)

appear to be the most bioavailable.

Mercury (Hg)

Mercury is a toxic substance which has no known function in human

biochemistry or physiology and does not occur naturally in living organisms.

Monomethylmercury is probably the most common toxic form of mercury found in

the marine environment. It has been known to travel through marine food chains

and causes damage to human consumers. All mercury that is released in the

environment will eventually end up in soils or surface waters.

2.1.3 Sediment Quality Guidelines

a. Ontario Ministry of Environment Screening Level Guidelines

The Ontario Ministry of Environment developed sediment quality

guidelines based on screening level concentrations from data for a range of local

sediments and benthic biota (ANZECC, 2000). The ministry had set three levels of

guidelines, the no-effect-level or NEL, the low-effect-level or LEL and the severe-

effect-level or SEL.

The NEL is point at which the chemicals in the sediments do not affect fish

or sediment-dwelling organisms. There is no expected effect on the water quality


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for there is no transfer of chemicals on the food chain. This level is considerably

clean. The LEL is the lowest that toxic effects become apparent and the SEL

represents concentrations that could effectively eliminate most of the benthic

organisms and pollutes the sediments. If the sediment is above SEL, testing must

be made to find out if the sediment is acutely toxic.

In line with the three levels of guidelines, the levels of contaminations for

possible metals and nutrient contents were set by Ontario Ministry of

Environment. Values are shown in Tables 2.1 and 2.2.

Table 2.1 Ontario Ministry of Screening Level Guidelines

Contaminant Lowest Effect

Level (ppm)

Severe Effect

Level (ppm)

Metals

Copper 16 110

Lead 31 250

Cadmium 0.6 10

Mercury 0.2 2


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Table 2.2 Ontario Sediment Quality Benchmarks

Nutrients Lowest Effect

Level (ppm)

Severe Effect

Level (ppm)

Total Phosphorus 600 2000

Total Kjeldahl Nitrogen 550 4800

Total Organic Carbon 1% 10%

The levels of effect are designed to help environmental managers determine:

when sediment may be considered clean;

what levels of contamination are acceptable for short periods of time while

the source of the contamination is being controlled and cleanup plans are

being developed;

what levels of contamination are considered severe enough to consider the

possibility of either removing the sediment or covering it with a layer or two

of cleaner sediment; This is called capping.

The three levels of effect are:

The No Effect Level: This is the level at which the chemicals in the

sediment do not affect fish or the sediment-dwelling organisms. At this level

no transfer of chemicals through the food chain and no effect on water

quality are expected.


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Sediment that has a No Effect Level rating is considered clean and no

management decisions are required. Furthermore, it may be placed in rivers

and lakes provided it does not physically affect the fish habitat or existing

water uses - for example a water intake pipe.

The Lowest Effect Level: This indicates a level of contamination which has

no effect on the majority of the sediment-dwelling organisms. The sediment

is clean to marginally polluted.

Dredged sediments containing concentrations of organic contaminants -

PCBs or pesticides, for example - that fall between the No Effect Level and

the Lowest Effect Level may not be disposed of in an area where the

sediment at the proposed disposal site has been rated at the No Effect Level

or better.

Contamination in sediment that exceeds the Lowest Effect Level may require

further testing and a management plan.

The Severe Effect Level: At this level, the sediment is considered heavily

polluted and likely to affect the health of sediment-dwelling organisms. If the

level of contamination exceeds the Severe Effect Level then testing is

required to determine whether or not the sediment is acutely toxic.

At the Severe Effect Level a management plan may be required. The plan

may include controlling the source of the contamination and removing the

sediment.

b. Hong Kong Sediment Quality Guideline

The Sediment Quality Guidelines of Hong Kong were primarily adopted or

modified from the United States and other temperate countries even though Hong


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Kong is located in the tropics. Hong Kong also has unique climate and hydrology

that make adopting SQGs from other countries not desirable. Unlike most tropical

countries, Hong Kong has marked seasonality with warm, wet summers and cold,

dry winters.

The Sediment Quality Guideline values were derived from an extensive

international database including effects range low (ERL), effects range median

(ERM), and the Puget Sound Estuary Program. The chemical classes currently

measured include metals, metalloids, PAHs, PCBs, and tributylin. Two SQGs were

developed for each chemical or class of chemicals. The lower chemical exceedance

level (LCEL) represents a value below which contaminants in the sediment are not

expected to have adverse biological effects, whereas the upper chemical

exceedance level (UCEL) represents a value above which toxicity is likely.

Table 2.3 Sediment quality guideline values Lower Concentration Exceedance

Level (LCEL) and Upper Concentration Exceedance Level (UCEL) of

Hong Kong

Contaminant Lower Chemical

Exceedance Level (ppm)

Upper Chemical

Exceedance Level

(ppm)

Metals

Lead 75 110

Mercury 0.5 1

Copper 65 270


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2.1.4 Bioremediation

Bioremediation can be defined as any process that uses microorganisms,

fungi, green plants or their enzymes to return the natural environment altered by

contaminants to its original condition. Aerobic Bioremediation is the practice of

adding oxygen to groundwater and/or soil to increase the number and vitality of

indigenous microorganisms performing biodegradation, calcium peroxide and

magnesium peroxide is often used as injection material.

The activity of naturally occurring microbes is stimulated by circulating

water-based solutions through contaminated soils to enhance in situ biological

degradation of organic contaminants or immobilization of inorganic contaminants.

Nutrients, oxygen, or other amendments may be used to enhance bioremediation

and contaminant desorption from subsurface materials.

Through bioremediation, soil lightly contaminated with petroleum

hydrocarbons is inoculated with a nutrient and an engineered bacterium that

combine to break down the contaminants. The bacteria access the nutrients, which

have attached to the hydrocarbons, and quickly and thoroughly degrade the

contaminants. The average time needed to reduce contaminants to acceptable

levels through bioremediation is approximately 7 to 14 days. The bioremediation

process provides substantial cost savings when compared to thermal desorption or

chemical fixation, and is typically used on soil with lower levels of contaminants.

Materials treated through bioremediation are typically beneficially re-used as fill

material.

Biological stimulants are often used to enhance the natural attenuation of

environmental contaminants. Bioremediation products are commercially used to

attenuate such contaminants as fuel hydrocarbon constituents and organic solvents


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that may be biologically transformed or immobilized under aerobic conditions. The

dissolved oxygen released from such products transforms/immobilizes the

contaminants. For this reason, a slow dissolved oxygen release is preferred to

increase contact with the contaminants dissolved in groundwater or adsorbed onto

the formation matrix. A fast release is ineffective when trying to remove the

contaminants. For example, magnesium peroxide / calcium peroxide is a potential

stimulant for contaminant attenuation. However, upon hydration these peroxides

tend to disassociate rapidly. In fact, magnesium/calcium peroxide can release their

entire dissolved oxygen load within a few weeks of hydration. For optimum use,

such stimulants must release dissolved oxygen slowly over a longer period of time,

on the order of months and not weeks. There are other compounds, such as MgO2,

CaO2, that slowly release oxygen when chemically bonded with phosphate. This

release of oxygen is a chemical process. Again, if the oxygen is released too fast,

the compound is useless as a bioremediation product. While chemically-bonded

products can solve the time-releasing problem, such compounds can be costly to

manufacture and use in large amounts. Magnesium Peroxide has the active oxygen

level as 10% commercially but Calcium Peroxide provides active oxygen level as

16%.

Bioremediation techniques have been successfully used to remediate soils,

sludge, and ground water contaminated with petroleum hydrocarbons, solvents,

pesticides, wood preservatives, and other organic chemicals.

2.1.5 Total Organic Carbon

Total organic carbon has a major influence on both the chemical and

biological process that take place in sediments. The amount of organic carbon has

a direct role in determining the redox potential in sediment, thus regulating the

behavior of other chemical species such as metals. Sources of organic carbon


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include organic matter from overland runoff and shoreline erosion (mostly

marshes), and primary productivity within the bays, all of which eventually settle

to the bay bottom and are incorporated into the sediment. Too much organic matter

can lead to the depletion of oxygen the sediment and overlying water, which can

have a deleterious effect on the benthic and fish communities. Total organic

carbon (TOC) content in sediments has been used as an indicator of pollution and

eutrophication rate (Folger 1972; EPA 2002).

2.1.6 Total Phosphorus

Phosphorus occurs naturally in rocks and other mineral deposits. During

the natural process of weathering, the rocks gradually release the phosphorus as

phosphate ions which are soluble in water and the mineralize phosphate

compounds breakdown. Phosphates are formed from this element. Phosphates

exist in three forms: orthophosphate, metaphosphate (or polyphosphate) and

organically bound phosphate each compound contains phosphorous in a different

chemical arrangement. These forms of phosphate occur in living and decaying

plant and animal remains, as free ions or weakly chemically bounded in aqueous

systems, chemically bounded to sediments and soils, or as mineralized compounds

in soil, rocks, and sediments.

Phosphorus is one of the key elements necessary for growth of plants and

animals and in lake ecosystems it tends to be the growth limiting nutrient. The

presence of phosphorus is often scarce in the well-oxygenated lake waters and

importantly, the low levels of phosphorus limit the production of freshwater

systems (Ricklefs, 1993).Unlike nitrogen, phosphate is retained in the soil by a

complex system of biological uptake, absorption, and mineralization. Phosphates

are not toxic to people or animals unless they are present in very high levels.

Digestive problems could occur from extremely high levels of phosphate. The


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soluble or bio-available phosphate is then used by plants and animals. The

phosphate becomes incorporated into the biological system but the key areas

include: ATP, DNA, and RNA; ATP, adenosine triphosphate, which is important

in the storage and use of energy and a key stage in the Kreb's Cycle. RNA and

DNA are the backbones of life on this planet, via genetics. Therefore the

availability of phosphorous is a key factor controlling photosynthesis.

Phosphate will stimulate the growth of plankton and aquatic plants which

provide food for larger organisms, including: zooplankton, fish, humans, and other

mammals. Plankton represents the base of the food chain. Initially, this increased

productivity will cause an increase in the fish population and overall biological

diversity of the system. But as the phosphate loading continues and there is a

build-up of phosphate in the lake or surface water ecosystem, the aging process of

lake or surface water ecosystem will be accelerated. The overproduction of lake or

water body can lead to an imbalance in the nutrient and material cycling process

(Ricklefs, 1993). Eutrophication (from the Greek - meaning "well nourished") is

enhanced production of primary producers resulting in reduced stability of the

ecosystem; excessive nutrient inputs, usually nitrogen and phosphate, have been

shown to be the main cause of eutrophication over the past 30 years. This aging

process can result in large fluctuations in the lake water quality and trophic status

and in some cases periodic blooms of cyanobacteria.

The non-point sources of phosphates include: natural decomposition of

rocks and minerals, stormwater runoff, agricultural runoff, erosion and

sedimentation, atmospheric deposition, and direct input by animals/wildlife;

whereas: point sources may include: wastewater treatment plants and permitted

industrial discharges. In general, the non-point source pollution typically is

significantly higher than the point sources of pollution. Therefore, the key to sound

management is to limit the input from both point and non-point sources of

phosphate.


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2.1.7 Total Kjeldahl Nitrogen

Nitrogen itself is not hazardous when present in water, and therefore does

not cause any environmental damage. In seawater nitrates, nitrites and ammonia

are dietary requirements for plankton, causing nitrogen concentrations to be lower

at the surface than in the deep. At increasing nitrogen concentrations in surface

layers, plankton production increases, leading to algal blooms. This may occur in

any type of surface water. Large amounts of nitrate may cause eutrophication,

which means an excess of nutrients resulting in oxygen deprivation and fish deaths

(see oxygen and water). Nitrogen does not limit algal growth, because phosphorus

is generally a limiting factor in water bodies. This means that phosphorus is the

determining factor of algal spreading through surface waters. Oxygen deficits in

surface water generally result in nitrate reduction to elementary nitrogen or nitrous

oxide.

Total Kjeldahl Nitrogen or TKN is the sum of organic nitrogen, ammonia

(NH3), and ammonium (NH4+) in the chemical analysis of soil, water, or

wastewater (e.g. sewage treatment plant effluent). To calculate Total Nitrogen

(TN), the concentrations of nitrate-N and nitrite-N are determined and added to

TKN.TKN is determined in the same manner as organic nitrogen, except that the

ammonia is not driven off before the digestion step.


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2.1.8 Equipment

Atomic Absorption Spectrophotometer (AAS)

Atomic Absorption Spectrophotometer is designed to determine the

presence and concentrations of metals in sediment samples. Metals include Cd, Cu,

Pb, and Hg, Cd. Typical concentrations range in the low mg/L (ppm) range. The

light of a specific wavelength is passed through the atomic vapor of an element of

interest, and measurement is made of the attenuation of the intensity of the light as

a result of absorption. Quantitative analysis by AA depends on the accurate

measurement of the intensity of the light and the assumption that the radiation

absorbed is proportional to atomic concentration. Metals will absorb ultraviolet

light in their elemental form when they are excited by heat, either by flame or

graphite furnace. Each metal has a characteristic wavelength that will be absorbed.

The AAS instrument looks for a particular metal by focusing a beam of UV light at

a specific wavelength through a flame and into a detector. The sample of interest is

aspirated into the flame. If that metal is present in the sample, it will absorb some

of the light, thus reducing its intensity. The instrument measures the change in

intensity. A computer data system converts the change in intensity into an

absorbance.


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2.2 Related Studies

Heavy Metal Contamination in Sediments

A study conducted by Sukiman B. Sarmani determines the heavy metals in

water, suspended materials and sediments from Langat River, Malaysia states the

distribution of heavy metals in the Langat River were studied for a period of six

months. Heavy metals such as arsenic, cadmium, cerium, cobalt, chromium,

cesium, lanthalium, rubidium, antimony scandium and zinc were determined in

water suspended materials and sediments samples from Langat River by neutron

activation and atomic absorption spectrometry.

A study was conducted by Ahmad et al. (2009) to determine the

concentration of selected heavy metals in Sungai Kelantan, Kelantan, Malaysia.

The river water quality was measured together with metal concentrations in

sediments in order to confirm to quality of the river. Result of water quality

analysis indicated that Sungai Kelantan is characterized by excellent water quality.

Total metal concentrations in sediment were lower as compared to the

concentration in earth crust for baseline concentration for heavy metals.

Dr. Walter Gossler and AnilaNeziri of University of Shkodra, Albania

conducted a study about the monitoring of heavy metals in water and sediment

samples from Drini River, Buna River and Lake Shkodra. From the results of

analysis of sediments from Shkodra Lake, River Drini and River Buna by using

two methods of extraction and analyzing them in ICP-MS for total concentration

of toxic metals as Copper and Cadmium, they concluded that sites in river Drini

and Buna are most contaminated from these metals which indicated in water

quality Shkodra lake and posted a risk for lake Buta. The most probable results are

geological construction from North Albania and the existing of the considerable

number of mines near Drini River.


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Nutrient Content of Sediments

Determination of total Phosphorus, total Nitrogen and Nitrogen Fractions

by Dr. Enno The task of this desk study is to give a survey over the existing

standards and the state of the art of the determination of total nitrogen (Dumas),

Kjeldahl nitrogen, the nitrogen fractions and total phosphorus. The evaluation of

the possibility of proposing draft standards for the fields of soil, sludge, bio waste

and related wastes for the respective nutrients should be the outcome. The

assessment of the existing standards shows that partly acceptable descriptions

exist. They are related to one field only e.g. soil or e.g. sludge. The different

materials require different proceedings and especially the homogeneity has to be

considered. The high demands on analytical quality and the respective validation

have to be satisfied. The result of this desk study is presented in four separate draft

standards for the determination of Kjeldahl nitrogen, total nitrogen (Dumas), the

extraction of nitrogen fractions and total phosphorus. The necessary work to

validate these standards to fulfill the high demands on analytical quality for all

applications described in the corresponding scope is pronounced.

Bioremediation

A review about Bioremediation has been argued to be one of the most cost-

effective remediation technologies available to reduce soil, sediment, or

groundwater contamination, particularly because this approach may allow for the

implementation of in-place strategies. This has been prepared by P. Adriaens, M.-

Y. Li and A. M. Michalak Recent entitled Scaling Methods of Sediment

Bioremediation Processes and Applications. Trends have advocated the application

of innovative sediment stabilization strategies through placement of (reactive)

capping material to allow long-term biodegradation of contaminants in these

complex biogeochemical environments. The potential long-term risk reduction


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associated with this approach requires a demonstration of causal relationships

between sediment or contaminant stability on the one hand, and microbial

reactivity on the other. The spatial analysis needed to fully understand and quantify

these correlations requires sensitive probabilistic techniques. This work will be

used to develop an uncertainty-based spatial decision tool for site remediation in

this watershed using various capping strategies.

A study entitled Developments in Bioremediation of Soils and Sediments

Polluted with Metals and Radionuclides by Henry H. Tabak, US EPA, ORD,

Environmental Research Center, National Risk Management Research Laboratory,

Land Remediation and Pollution Control Division, Cincinnati and Terry C. Hazen,

Lawrence Berkeley National Laboratory, Virtual Institute for Microbial Stress and

Survival, Earth Sciences Division, Ecology Dept. Berkeley. This paper will

provide a review of published research on field studies on bioremediation of metal

and radionuclide contaminated soils and sediments. The paper will (1) cite

examples of field research and cases of field in-situ bioremediation of metal and

radionuclide contaminated soils and sediments; (2) discuss the role of

phytoremediation in the treatment of metal and radionuclide contaminated soils;

and (3) provide information on the use and field-scale application of surfactants in

the treatment of metal and radionuclide pollution of soils and sediments. The

following metal-microbe interactions that impact bioremediation of metal

contamination in soils and that can be applied to field-scale biotreatment will be

discussed: Biotransformation (bioreduction and biooxidation); (2) bioaccumulation

and biosorption; (3) biodegradation of chelators; (4) biosurfactants and

biologically-assisted soil washing; (5) volatilization; and (6) biotreatment trains

and natural attenuation. The paper will also discuss research on the treatment of

metal contaminated soils, wetlands and mine areas with the use of biosolids, by

providing information on (1) in-situ soil treatments to reduce phyto- and

bioavailability of metals and (2) the use of biosolids to restore metal contaminated

mining areas impacted by metal tailings. The last 15 years have seen an increase in


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the types of contaminants to which bioremediation is being applied, including

solvents, PAHs and PCBs. Now, microbial processes are beginning to be used in

the cleanup of radioactive and metallic contaminants of soils and sediments.

Microorganisms can interact with these contaminants and transform them from one

chemical form to another by changing their oxidation state through the addition of

(reduction) or moving (oxidation) of electrons.

In some bioremediation strategies, the solubility of the transformed metal

or radionuclide increases, thus increasing the mobility of these contaminants and

allowing them to more easily be flushed out from the environment. In other

strategies, the transformed metal or radionuclide may precipitate out of the

solution, leading to immobilization. Both kinds of transformations present

opportunities for bioremediation of metals and radionuclides in the environments;

either to immobilize or to accelerate their removal. Metal contamination of soils

and sediments is especially problematic because of the strong adsorption of many

metals to their particles. Due to the difficulty of desorbing metal contaminants,

some traditional remediation methods, simply immobilize metals in contaminated

soils, by the addition of cement or chemical fixatives, by capping with asphalt, or

by in-situ vitrification. Alternatively, soils are often isolated by excavation and

confinement in hazardous waste facilities. Although rapid in effect, both of these

options are expensive and destroy soil’s future productivity. The success of soil

washing and pump-and-treat technologies to remove metals is severely limited by

the slow desorption kinetics of adsorbed metals, with the result that additional

additives (acids, chelates and reductants) are often used to promote metal transfer

to the aqueous phase. These agents improve cost effectiveness but may introduce

further harmful chemicals. A primary strategy of bioremediation is the use of

similar metal-immobilizing agents in conjunction with soil washing, with

advantage that they pose no known environmental threat themselves. Biopolymers

have been discovered that bind metals with high affinity and travel relatively

unimpeded through porous medium. Certain microorganisms transform strongly-


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adsorbing metal species into more soluble forms and plants are being recruited that

act as self-contained pump-and-treat systems. Other methods employ enzymatic

activities to transform metal species into volatile, less toxic or insoluble forms.

Techniques for soil bioremediation are usually designed to be used in-situ,

lowering costs; they avoid the use of toxic chemicals and in nearly all cases, the

soil structure and potential for productivity are preserved.

Accumulation Rate of Sediments

A study entitled Estimating accumulation rates in manila Bay, a marine

pollution hot spot in the Seas of East Asia Study by E.Z. Sombrito,A.dM,

Bulos,F.P. Siringan and E.J. Sta Maria, they identify Manila Bay as among the

marine pollution hot spots in the East Asia. Pb lead dating of its sediments can

provide a historical perspective of its pollution loading. However, the validity of

Pb dating in a complex dynamic coastal system of Manila Bay may come into

Questions. Land-based sediment input can be high and physical and biological

processes can possibly disturb the sediment layers. In this report, the Pb profiles of

sediment core from different parts of the variable across the bay. The largest

change in sedimentation rate coincided with the occurrence of a volcanic eruption

in 1991 and is shown by applying a variant of the CIC model in sedimentation rate

calculations. The data suggest that Pb dating can be very useful in estimating

relative magnitudes of sedimentation rates, even in a complex dynamic coastal

system like Manila Bay.


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CHAPTER 3

METHODOLOGY

3.1 Description of Study Area

Bioremediation chambers are located along Estero de Balete. The three

chambers are 5.7 ft high and have an area of about 222.71 ft2.

Figure 3.1a Bioremediation

Chambers


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Experimental Design

3.2 Preparation of Sampling Bed and Containers

Sampling bed are composed of frame made of a wood 1 ft. by 1 ft. dimensions

and the filter bed made of filter cloth (katsa), assembled manually. The filter beds are

weighed individually in a Top Load Balance. Containers for sediments subjected to

heavy metal analysis were cleaned by washing with distilled water.

Figure 3.1b Experimental Design for the Determination of

Accumulation Rate

CHAMBER

2

SEDIMENTS

CHAMBER

1

POINT

1 POINT

2

POINT

3

POINT

1 POINT

2

POINT

3

Figure 3.2 Sampling Bed

Wood Frame

1 ft by 1 ft

Filter

Bed

1 in


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Figure 3.3 Sampling Points for Determination of Accumulation Rate

Chamber 2

8 ft 1 in

14 ft 7 in

Chamber 1

●

●

●

8 ft 1 in

14 ft 8 in

●

●

●

3.3 Selection of Sampling Site

Sampling beds were diagonally arranged in the chamber as shown in Figure 5.

The filter beds were placed before the treatment process.

3.4 Collection of Sediment Samples

For the determination of accumulation rate of sediments, samples were taken

from each chamber every 22 days in a 2-month period, as water from each chamber is

transferred from one chamber to another every month. Filter beds were lifted up when

the water level is already about one foot above the ground of the chamber. The cloth,

which contains the sediments, was sun dried and then weighed.

Sediments, which are subjected for the analysis of heavy metal content and

nutrient content, were collected by getting samples from random sites within the

chamber. Samples, in the form of sludge, were placed in pet bottles. Overlying water

was eliminated from the pet bottle. All samples were kept at 4°C and then sent to a

DENR accredited private laboratory for analysis.

The following methods were used by the government accredited private

laboratory for the sediment analysis:


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Table 3.4 Methods Used for the Analysis of Total Phosphorus, Total Organic

Carbon, Total Nitrogen and Heavy Metals

Contaminant Method Used

Heavy Metals

Copper Flame AAS

Cadmium Flame AAS

Lead Flame AAS

Mercury Manual Cold Vapor AAS

Nutrient Content

Total Organic Carbon Ascorbic Acid Method/

Titrimetric Method

Total Phosphorus Stannous Chloride Method/

Titrimetric Method

Total Kjeldahl Nitrogen Kjeldahl Method


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CHAPTER 4

DATA PRESENTATION, ANALYSIS AND INTERPRETATION OF RESULTS

The data obtained from the experiment were presented, analyzed and

interpreted in this chapter to determine the effect of the bioremediation treatment on

the physical and chemical properties of sediments of Estero de Balete. The results of

analyses from the second run of the test were analyzed here because more considerable

change on the properties of sediments was observed than in the first run.

4.1 Physical Properties of Collected Sediments

The sediments collected from the chamber, using Powder Dispersion Method,

was observed to have light greenish gray color while the sediments from the chamber,

using Tea Bag Method, have dark greenish gray color. The light color in the Powder

Dispersion Method was mainly due to the presence of unmixed biominerals in the

collected sediments. The odor of sediments collected from the chamber both have

“fishy” odor. The odor may be attributed to the occurrence of algae buildup inside the

chamber.

Physical

Property

Powder Dispersion Method

(Chamber 1)

Tea Bag Method

(Chamber 2)

Color Light Greenish

gray

Dark greenish

gray

Odor Fishy Fishy

Table 4.1 Physical Properties of Collected Sediments


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7.7

2.4 2.5

ND 0.1 ND ND ND 0

1

2

3

4

5

6

7

8

9

Powder Dispersion Method Tea Bag Method

Co

nce

ntr

atio

n (

pp

m)

Copper Lead Cadmium Mercury

ND - Not Detected (below reporting limits)

4.2 Heavy Metal Concentrations of Collected Sediments

Heavy metals which are in high concentrations are toxic to plants and animals.

Figure 4.2 shows the heavy metal concentrations of the collected sediments after

undergoing bioremediation treatment.

The results show a decrease in the heavy metal content after the treatment.

Copper content was reduced by 70%. Cadmium and lead after Tea Bag Method were

below the reporting limits. This means that amounts of cadmium and lead are

insignificant and thus, it can be concluded that the collected sediments had negligible

amounts of the cadmium and lead after the remediation. Mercury contents were also

found to be below the reporting limits right after the first treatment. This could mean

that the sediments from the Estero de Balete hold a very small amount of mercury.

The decrease in the heavy metal content can mainly be attributed to the

reaction occurred between the biominerals and the heavy metal species in the

Figure 4.2 Graphical Representation of Heavy Metal Concentrations of

Collected Sediments


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54

37

24

2.7 1.23 0.84

0

10

20

30

40

50

60

Powder Dispersion Method Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Total Kjeldahl Nitrogen Total Organic Carbon Total Phosphorus

sediments. In the first treatment, the biominerals were in direct contact with the

sediments. This caused the heavy metals to precipitate and coagulate inside the

chamber. The particles that built up were then settled at the bottom. Apparently, when

the wastewater was transferred to the second chamber, lesser amount of sediments had

come with. Therefore, as expected, heavy metal analysis for the first method would be

much higher than for the second.

4.3 Nutrient Content of Collected Sediments

Nutrients in sediments such as Total Organic Carbon, Total Kjeldahl Nitrogen

and Total Phosphorus are essential in the growth of organisms. However, excess

amount of these nutrients in a waterway can lead to low levels of dissolved oxygen

and negatively alter various plant life and organisms. In this study, the nutrient

contents are tested to show the effectiveness of the ORC used in reducing excessive

amounts of nutrients in sediments.

Figure 4.3 Graphical Representation of Nutrient Concentrations of

Collected Sediments


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110

16 7.7

2.4

0

20

40

60

80

100

120

SEL LEL Powder Dispersion

Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Copper

Figure 4.3 shows the concentrations of Total Nitrogen, Total Phosphorus, and

Total Organic Carbon concentrations after the treatment. Decrease in the nutrient

content was observed after using the two methods. Total Nitrogen and Total

Phosphorus contents were both reduced by just about 32% and the Total Organic

Carbon contents were reduced by 89%.

4.4 Assessment of Collected Sediments using Sediment Quality Guidelines

4.4.1 Ontario Ministry Sediment Quality Guideline

The purpose of the Ontario Ministry Sediment Quality Guidelines is to

protect the aquatic environment by setting safe levels for metals, nutrients

(substances which promote the growth of algae) and organic compounds. The

comparisons of the concentrations of contaminants in the sediments collected with

the Ontario Ministry Sediment Quality Guidelines are shown below.

Figure 4.4a Comparison of Copper Concentration from the



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250

31

2.5 ND 0

50

100

150

200

250

300


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Lead


Figures 4.4a shows the comparison of copper concentrations from the

collected sediments with Ontario Sediment Quality Guidelines. Copper in

sediments and in water in is usually associated with tubing & plumbing which

water comes into contact with. The figure shows that the concentrations of copper

after the treatment were below the LEL value of Ontario Sediment Quality

Guidelines which means that it cause no serious effect to the environment.

Figure 4.4b describes the comparison of lead concentrations from

sediments collected with the Ontario Sediment Quality Guidelines. Lead, a metal

found in natural deposits, is commonly found on some consumer products such as

paint and children’s toys. Lead contamination may be caused by disposal of lead-

containing objects to Estero de Balete. The figure above shows that concentrations

of lead were below the LEL values of Ontario Sediment Quality Guidelines.

Hence, lead concentrations after the treatment pose no threat to the surroundings.

Figure 4.4b Comparison of Lead Concentration from the Collected



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10

0.6 0.1 ND

0

2

4

6

8

10

12


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Cadmium


Figure 4.4c represents the comparison of cadmium concentrations tested

with the LEL and SEL values of Ontario Sediment Quality Guidelines. Cadmium

is a natural, usually minor constituent of surface and groundwater. Cadmium

contamination may be caused by weathering and erosion of soils and bedrock and

improper disposal of cadmium-containing waste. Based on the figure,

concentrations of cadmium after treatment were lower than the LEL value of

Ontario Sediment Quality Guidelines. Thus, cadmium concentration can be

considered to present little or no ecological effects.

Figure 4.4c Comparison of Cadmium Concentration from the



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2

0.2

ND ND 0

0.5

1

1.5

2

2.5


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Mercury


Figure 4.4d describes the comparison of mercury concentrations of the

sediments collected with Ontario Sediment Quality Guidelines. It shows that

concentrations of mercury were insignificant after treatment so, apparently,

mercury concentrations were below the LEL values and therefore, it pose no

serious threat in the surrounding.

In brief, heavy metal concentrations were below the Low and Severe Effect

Levels of Ontario Ministry Sediment Quality Guideline. This means that the

collected sediments now have a No Effect Level rating. Therefore, the sediments

are now considered clean and no management decisions are required. The OMSQ

Guideline suggests that the sediments in Estero de Balete may be placed in rivers

and lakes provided it does not physically affect the fish habitat or existing water

uses.

Figure 4.4d Comparison of Mercury Concentration from the



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4800

550

54 37 0

1000

2000

3000

4000

5000

6000


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Total Kjeldahl Nitrogen

2000

600

1.23 0.84 0

500

1000

1500

2000

2500


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Total Phosphorus

Figure 4.4e Comparison of Total Kjeldahl Nitrogen Concentration

from the Collected Sediments with Ontario Sediment Quality

Guidelines

Figure 4.4f Comparison of Total Phosphorus Concentration from

the Collected Sediments with Ontario Sediment Quality Guidelines


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100000

10000

24 2.7 0

20000

40000

60000

80000

100000

120000


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Total Organic Carbon

Figures 4.4d, 4.4e and 4.4f describe the comparison of Total Kjeldahl

Nitrogen, Total Phosphorus and Total Organic Carbon concentrations of the

sediments collected after the treatment with the Ontario Sediment Quality

Guidelines. Nutrient concentrations were below the Lowest Effect Level values of

the Ontario Sediment Quality Guideline. Therefore, the nutrient concentrations

after the treatment have no effect on water quality.

Figure 4.4g Comparison of Total Organic Carbon Concentration

from the Collected Sediments with Ontario Sediment Quality

Guidelines


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270

65

7.7 2.4 0

50

100

150

200

250

300

UCEL LCEL Powder Dispersion

Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Copper

ND - Not Detected (Below Reporting Limits)

4.4.2 Hong Kong Sediment Quality Guideline

The sediment quality, according to its level of toxicity, is determined with

the use of the Hong Kong Sediment Quality Guideline. Analyses using this

guideline are as follows.

Copper concentrations found on the collected sediments were below the

LCEL of the Hong Kong sediment quality guideline s shown in Figure 4.4h. This

implies that copper content after treatment are not expected to have adverse

biological effects.

Figure 4.4h Comparison of Copper Concentration from the

Collected Sediments with Hong Kong Sediment Quality Guideline


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110

75

2.5 ND 0

20

40

60

80

100

120


Method

Tea Bag Method

Co

nce

ntr

ati

on

(p

pm

)

Lead


Figure 4.4i shows the comparison of lead concentration from the sediments

collected with Hong Kong Sediment Quality Guideline. Amount of lead after the

treatment were below 75 ppm which is the LCEL value of Hong Kong Sediment

Quality Guideline. Thus, the lead concentrations are not expected to cause

unfavorable environmental effects.

Figure 4.4i Comparison of Lead Concentration from the Collected

Sediments with Hong Kong Sediment Quality Guideline


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1

0.5

ND ND 0

0.2

0.4

0.6

0.8

1

1.2


Method

Tea Bag Method

Co

ncen

tra

tio

n (

pp

m)

Mercury


Figure 4.4i shows the comparison of lead concentration from the sediments

collected with Hong Kong Sediment Quality Guideline. Detected amounts of

mercury were too small after the treatment. Perceptibly, the concentrations of

mercury were below the LCEL value of the Hong Kong sediment quality guideline

which means that adverse biological effects are doubtful.

Figure 4.4j Comparison of Mercury Concentration from the

Collected Sediments with Hong Kong Sediment Quality Guideline


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4.5 Accumulation Rate of Sediments

Table 4.5 shows the accumulation rate of sediments in chamber 1 (Powder

Dispersion Method) and chamber 2 (Tea Bag Method). As expected, the accumulation

rate in chamber 1 is higher than chamber 2. This is evident since chamber 1 contains

more amounts of sediments. In chamber 1, sediments were mixed up with the

dispersed biominerals. Consequently, large particles were formed and settled at the

bottom. Larger particles are more likely to have faster settling rate. Given that the

biominerals used in chamber 2 were not in direct contact with the sediments, it can be

concluded that sediments in this chamber has smaller particle size. Therefore, it would

have lesser settling rate.

Method Used

1st Run

2nd

Run

Average

Powder

Method

596.05 mg/ m2 ·

hr

294.82 mg/ m2·

hr

445.4 mg/ m2·

hr

Tea Bag

Method

-

30.89 mg/ m2·

hr

30.89 mg/ m2·

hr

Table 4.4: Average weight of sediments in each filter bed

Table 4.5 Accumulation Rate of Sediments in each Filter Bed per Unit Area


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CHAPTER 5

SUMMARY OF FINDINGS, CONCLUSIONS AND RECOMMENDATIONS

5.1 Summary of Findings

The sediment samples collected were subjected to metals and nutrient

content analysis done by a government accredited laboratory. Table 5.1 shows the

summary of contaminant analyses in comparison with the two Sediment Quality

Guidelines: Ontario Sediment Quality Guidelines and Hong Kong Sediment

Quality Guideline.

*ND – Not Detected (Below Reporting Limits)

Contaminant

Method Used

Cu Pb Cd Hg TKN TP TOC

Powder Method 7.7 2.5 0.10 ND* 54 1.23 24

Tea Bag Method 2.4 ND ND ND 37 0.84 2.7

Ontario

Sediment

Quality

Guidelines

Lowest 16 31 0.6 0.2 550 600 1%

Severe 110 250 10 2 4800 2000 10%

Hong Kong

Sediment

Quality

Guideline

LCEL 65 75 - 0.5 - - -

UCEL 270 110 - 1 - - -

Table 5.1 Concentrations of Lead, Mercury, Copper, Cadmium and Nutrients from

Sediments Collected after the Bioremediation Treatment and from

Sediment Quality Guidelines (ppm)


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5.2 Conclusions

The accumulated sediments in the treatment chambers were observed to

have greenish gray color and have a fishy odor. This observation can mainly be

attributed to the algae growth as the remediation goes on.

Based on the results obtained, the mean heavy metal levels after the

remediation test provided an array of Cu>Pb>Cd>Hg. After the treatment,

significant amounts of Copper in sediments were still present while the presence of

Lead, Cadmium and Mercury was not detected. The concentrations of all the metal

contaminant are below the Lowest Effect Level values of Ontario Sediment

Quality Guidelines and Lower Concentration Exceedance Level values of Hong

Kong Sediment Quality Guideline. Therefore, these metals pose no significant

effect to the environment and adverse biological effects are very much doubtful.

Also, the nutrient concentrations of the collected sediments are found to be

of favorable amounts. After the treatment, the concentrations of Total Kjeldahl

Nitrogen, Total Phosphorus and Total Organic Carbon are below the lower

threshold limits of Ontario Sediment Quality Guidelines and Hong Kong Sediment

Quality Guideline. Thus, these nutrients pose no serious threat to the surrounding.

The average accumulation rate of the sediments in the first (Powder

Dispersion Method) and second (Tea Bag Method) chamber was found to be 445.4

mg/m2•h and 30.89 mg/m

2•h, respectively.


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5.3 Recommendations

Based on the observations, we recommend a further study on the copper

content of the sediments from estero. Even though the copper concentrations were

below the lower threshold limit of the sediment quality guidelines, a

comprehensive outline of its source must be provided. Further research on how the

copper content will completely remove from the sediments must be done.

It is recommended to identify the presence of other heavy metals such as

chromium and zinc to verify the quality of the treated sediments. Also, other

properties of the sediments such as Polychlorinated Biphenyls (PCBs) must be part

of future studies.

It is also recommended to run more trials to validate the efficiency of the

bio-remediation medium used.

Further research on other remediation techniques must be done so we can

provide evidence that Estero de Balete still holds its hope for the existence of

future biodiversity.


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APPENDICES

Appendix A: Results of Analyses

Run 1

Date of Sampling: December 17, 2010

Test Description Results Units Reporting

Limits Test Methods

Chamber 1 (Powder Dispersion Method)

Cadmium ND* mg/L 0.01 Flame AAS

Copper 9.9 mg/L 0.04 Flame AAS

Lead ND mg/L 0.07 Flame AAS

Mercury 0.03 mg/L 0.0002 Manual Cold

Vapor AAS

Total Kjeldahl

Nitrogen 36 mg/L 1.0

Titrimetry

(Kjeldahl Method)

Phosphate-P 2.0 mg/L 0.05 Stannous Chloride

Method

Total Organic Carbon 4.87 % w/w 0.10 Titrimetry

Chamber 2 (Tea Bag Method)

Cadmium ND mg/kg 0.20 Flame AAS

Copper 0.52 mg/kg 0.80 Flame AAS

Lead ND mg/kg 1.4 Flame AAS

Mercury 0.03 mg/kg 0.007 Manual Cold

Vapor AAS

Total Kjeldahl


Titrimetry

(Kjeldahl Method)


Method


*ND = Not Detected (Below Reporting Limits)


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Run 2

Date of Sampling: January 28, 2011

Test Description Results Units Reporting

Limits Test Methods

Chamber 1 (Powder Dispersion Method)

Cadmium 0.1 mg/L 0.01 Flame AAS

Copper 7.7 mg/L 0.04 Flame AAS

Lead 2.5 mg/L 0.07 Flame AAS

Mercury ND* mg/L 0.10 Manual Cold

Vapor AAS

Total Kjeldahl


Titrimetry

(Kjeldahl Method)

Phosphate-P 24 mg/L 2.0 Stannous Chloride

Method


Chamber 2 (Tea Bag Method)

Cadmium ND mg/kg 0.20 Flame AAS

Copper 2.4 mg/kg 0.80 Flame AAS

Lead ND mg/kg 1.4 Flame AAS

Mercury ND mg/kg 0.1 Manual Cold

Vapor AAS

Total Kjeldahl


Titrimetry

(Kjeldahl Method)


Method


*ND = Not Detected (Below Reporting Limits)


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Appendix B: Calculation of Accumulation Rate of Collected Sediments

Treatment Chamber Weight of Sediments (grams)

Chamber 1

(Powder Dispersion Method)

Area = 0.5056 m2

48.7 14.3 22.9

Chamber 2

(Tea Bag Method)

Area = 0.5781 m2

2.2 3.8 3.0

Treatment Chamber Weight of Sediments (grams)

Chamber 1

(Powder Dispersion Method)

Area = 0.5056 m2

88.7 61.4 9.02

Table B.2 Weight of Sediment Samples in Each Filter Bed (Second Run)

Table B.1 Weight of Sediment Samples in Each Filter Bed (First Run)


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First Run:

Chamber 1

( )

Second Run:

Chamber 1

( )

Chamber 2

( )


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Appendix C: Research Images

Treatment Chamber


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\

Collection of Filter Beds


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Sediment Sample

Sediment Sampling


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Storage of Sample


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The Researchers


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Appendix D: References

A. Books

Mudroch A, Azcue JM & Mudroch P 1997. Manual of Physico-chemical Analysis of

Aquatic Sediments. Lewis Publishers, Boca Raton, FL.

USEPA. 2005. Contaminated Sediment Remediation Guidance for Hazardous Waste

Sites, EPA-540-R-05-012. Office of Superfund Remediation and Technology

Innovation, 236 pp.

USEPA. 1999. Introduction to Contaminated Sediments. EPA 823-F-99-006, Office of

Science and Technology, 24 pp.

S.L. Simpson, 2005, Handbook for Sediment Quality Assessment.

B. Journals

García-Villalobos, Francisco Javier, Distribution of Total Organic Carbon and Total

Nitrogen in Deep-Sea Sediments from the southwestern Gulf of Mexico.

Gossler, W. And Neziri, A., Determination of heavy metals in water and sediments of

Drini River, Buna River and lake Shkodra, 2002

Johengen, T., Standard Operating Procedures for Determining Total Phosphorus,

Available Phosphorus, and Biogenic Silica Concentrations of Lake Michigan

Sediments And Sediment Trap Material


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Prudente M., Ichihashi H., and Tatsukawa Ryo., 1994. Heavy Metal Concentrations in

Sediments from Manila Bay, Philippines and Inflowing Rivers.

Riba I., DelValls T.A., Forja J.M., Go´mez-Parra, A., 2002. Influence of the

Aznalco´llar mining spill on the vertical distribution of heavy metals in

sediments from the Guadalquivir estuary (SW Spain). Mar. Pollut. Bull. 44,

39–47.

Sta. Maria E.J., Siringan F.P., BulosA.dM. And Sombrito E.Z., 2009.Estimating

sediment accumulation rates in Manila Bay, a marine pollution hot spot in the

Seas of East Asia.

Sombrito, E.Z., Siringan, F.P., and Sta.Maria,E.J., Estimating sediment accumulation

rates in Manila Bay, a marine pollution hot spot in the Seas of East Asia,

Marine Pollution Bulletin,2009

C. Electronic Sources

Brian A. Schumacher, Ph.D., Methods for the determination of Total Organic Carbon

(TOC) in soils and sediments, Retrieved September 29, 2010, from

http://www.epa.gov/esd/cmb/research/papers/bs116.pdf

Delia, C.F. et al "Nitrogen and Phosphorus Determinations in Estuarine Waters: A

Comparison of Methods Used in Chesapeake Bay Monitoring", Report

prepared for Chesapeake Bay Program Liaison Office, Region III, US EPA,

Annapolis, MD. 1987.

Exeter Analytical, Inc., Retrieved September 29, 2010, from

http://www.exeteranalytical.com/tn210.htm


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Potential Sources of Contamination. Retrieved January 29, 2011 from

http://www.njdwsc.com/prbwmp/wma3/doc/wca_report/wma3wca_3-1.pdf

USGS Bear Lake Project, 1998, Retrieved September 29, 2010, from

http://esp.cr.usgs.gov/info/lacs/lead.htm

Technical Guidance for Screening contaminated Sediments, 1999, Retrieved

September 29, 2010, from

http://www.dec.ny.gov/docs/wildlife_pdf/seddoc.pdf


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Banta, Mhadel Arguelles Address: 1627 Receiver 1st St. Phase 4, CAA Compound

Las Piñas City, Metro Manila

Mobile: +639463151634

E-Mail: [email protected]

OBJECTIVE: To offer my service and my talent to the best of my ability to a

professional organization and share my knowledge in Chemical

Engineering promoting team approach for the success of

organization.

EDUCATION:

School/Location Inclusive Date Degree

Adamson University 2006-Present BS ChE

Ermita, Manila

Rizal Technological University 2003-2004 BS ECE

Mandaluyong City

Parañaque National High School 1999-2003 Secondary

Parañaque City

Baclaran Elementary School Central 1993-1999 Elementary

Parañaque City

SPECIAL SKILLS: Computer Literate (Ms Word, Ms Excel, Auto-CAD)

Good in oral and written communication

Persuasive and hardworking

WORK EXPERIENCE: Date SERVICE CREW Nov. 2005 – April 2006

Jollibee Food Corporation

Zapote, Las Piñas City

SERVICE CREW April 2005 – Oct. 2005

Jollibee Food Corporation

Baclaran Terminal, Parañaque City


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Personal Vitae:

Sex : Female

Date of Birth : January 11, 1987

Place of Birth : Batangas

Civil Status : Single

Nationality : Filipino

Languages : Filipino & English

Affiliations:

Philippine Institute of Chemical Engineers (PIChE), Member

Adamson University Chemical Engineering Student Society

(AdUChESS), Member

Physics Society of Adamson University (PSAU), Member

CHARACTER REFERENCES:


Chairperson, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410 Engr. Jerry G. Olay

Faculty Member, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410

I hereby certify that the information above is true and correct to the best interest of my

knowledge.

ARGUELLES BANTA

Applicant


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Camille G. Candelaria 8 Doña Juana Subd. 3 Santolan Pasig city 1610 (+63)927-300-8208 [email protected]

Objective

To seek a challenging and rewarding opportunity where I can fully utilize my skills and experiences gained from my education and seminars

Education

Tertiary Adamson University

2006 - present

900 San Marcelino St., Ermita Manila B.S., Chemical Engineering

University Of Nueva Caceres June 2004-March 2006 Jaime Hernandez Avenue Naga City B.S., Electrical Engineering

Secondary

University of Nueva Caceres 2000 - 2004 Jaime Hernandez Avenue Naga City Graduation date: March 2004

Primary

University of Nueva Caceres 1994 - 2000

Jaime Hernandez Avenue Naga City Graduation date: March 2000

Personal Information

Birthday: April 16, 1987 Status: Single Citizenship Filipino Religion: Catholic Skills: Good communication Skills Computer litera

mailto:[email protected]


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I hereby swear that the above information is true.

Candelaria, Camille G. Applicant

Affiliates

Secretary, Womens Club (UNC Chapter) Secretary, LigangNagkakaisang Mag-aaral Para saAktibongPamunuan (LINGAP Member, Philippine Institute of Chemical Engineers (PIChE)

Member, Adamson University Chemical Engineering Student Society (AdUChESS)

Member, Physics Society of Adamson University (PSAU)

References

Engr. Merlinda Palencia

Chairperson, chemical Engineering Department Adamson University

Engr. Jerry Olay

Professor Adamson University

Melinda Candelaria Production Supervisor Ashford Pharmaceutical Laboratory Inc.


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Pagasartonga, Mon Eric P. #18 Gerodias St., San Vicente, San Pedro, Laguna 0927-6962880 [email protected] Objective: To have the opportunity to have hands-on experience on the theoretical concepts that I have learned, familiarizing me with the various industrial operations and unit process Personal Vitae

Age: 21

Sex: Male

Date of Birth: March 30, 1990

Place of Birth: San Pedro, Laguna

Nationality: Filipino

Civil Status: Single

Height: 5’5”

Weight: 117 lbs

Educational Background

School Year Graduated

B.S. Chemical

Engineering

Adamson University

900 San Marcelino St., Ermita, Manila

Secondary San Francisco de Sales School

101 National Highway, San Pedro,

Laguna

2006

Primary San Pedro Central School

San Pedro, Laguna

2002

Affiliations

Philippine Institute of Chemical Engineers (PIChE), Member

Adamson University Chemical Engineering Student Society (AdUChESS),

Member



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Skills

Computer Literate (knowledgeable in Microsoft Office Applications)

Willing to learn

Character References April M. Patricio, R.Ph.

Pharmacist Generika Drugstore, Montillano, Alabang 0916-3244678


Chairperson, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410

Engr. Jerry G. Olay

Faculty Member, Chemical Engineering Department Adamson University (632) 524-2011 loc. 410

I hereby certify that the information above is true and correct to the best interest of my knowledge.

MON ERIC PAGASARTONGA


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Ricarte, Shienah Coronado Blk.4 Lot 19 Palmera Springs 3-B, Camarin, Caloocan City

Email: [email protected] Mobile No.: 0935-9849828

Objective:

To have a challenging position in chemical engineering where I could apply all major principles and my specialized interested areas of application namely thermodynamics, fluid dynamics by which I can apply my wide knowledge and professional expertise in the field of chemical engineering.

Educational Attainment:

Adamson University

Ermita, Manila Bachelor of Science in Chemical Engineering 2004-present

St.Clare College of Caloocan

Zabarte rd.,Camarin Caloocan City

High School Graduate (3rd honour) 2001-2004

Bagong Silang Elementary

Elementary Graduate 1995-2000

Work Experience:

Grand Asia Food Corporation (Jollibee-Zabarte)

588 Camarin corner Zabarte Road (North), Caloocan City Administrative Crew July-December 2006

LOJ Food Corporation (Jollibee-Nova Quirino)

938 Quirino Highway, Novaliches, QC Service Crew December-May 2007

Achievements and Skills:

Adamson University Chemical Engineering Students Society (AdUChESS),

Member


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Liga ng Nagkakaisang Mag-aaral tungo sa aktibong Pamunuan

(LINGAP),Secretary


10th Outstanding Student for the School Year 2007-2008

(Chemical engineering Department)

Adamson University Academic Scholar Grantee (2nd sem,2007-2008)

Good computer skills (MS Office Applications and the Internet)

Outgoing, Persistent and Articulate

Willing to learn

Eager to contribute and be motivated to succeed

Personal Data: Age : 23 years old Gender: Female Citizenship : Filipino Civil Status: Single Birth date : January 23, 1987 Birth Place: Manila Height : 5’1 Weight: 90 lbs. Language : English, Tagalog Father’s name : Leonardo U. Ricarte Occupation: OFW Mother’s name: Ma.Rowena C. Ricarte Occupation: Teacher & Real State Dealer Sibling’s name: Ma. Sheila C. Ricarte Sarah Hazel C. Ricarte

Ma.Sheilinah C. Ricarte John Gerald C. Ricarte

Reference:

Engr.Jerry G. Olay

Professor, Chemical Engineering Department Adamson University

Beverly C. Samia

Bureau of Internal Revenue

Engr.Rommel Galvan

Professor, Chemical Engineering Department Adamson University I hereby swear that the above information is true.

Shienah Ricarte

characterization of accumulated sediments in bio-remediation chamber at estero de balete

Documents

research study

sediments assessment

mercury of sediments

study significance

study scope

sediments nutrient content

balete banta

background of study