OCS Study MMS 2004-031 

ANIMIDA Task 7 

 Partitioning of Potential Anthropogenic Chemicals 

between Dissolved and Particulate Phases in Arctic 

Rivers and the Coastal Beaufort Sea 

Final Report Submitted to 

 U.S. Department of Interior 

Minerals Management Service 

Anchorage, Alaska 

May 2004

Submitted by 

John H. Trefry, Robert D. Rember, Robert P. Trocine 

Florida Institute of Technology, Melbourne, Florida 

John S. Brown, Battelle, Waltham, Massachusetts 

Contract No. 143501-99-CT-30998, TO 10907 

 U.S. Department of the Interior 

 Minerals Management Service

 Alaska Outer Continental Shelf Region 
ii

ANIMIDA Task 7 

Partitioning of Potential Anthropogenic Chemicals between 

Dissolved and Particulate Phases in Arctic Rivers and the 

Coastal Beaufort Sea 

 

Final Report 

Submitted by: 

John H. Trefry, Robert D. Rember, Robert P. Trocine 

Department of Marine & Environmental Systems 

Florida Institute of Technology 

150 West University Boulevard, Melbourne, Florida, 32901 

John S. Brown, Battelle, 255 Bear Hill Road, 

Waltham, Massachusetts 02451 

(e-mail address for corresponding author: jtrefry@fit.edu) 

This study was funded by the U.S. Department of the Interior, 

Minerals Management Service (MMS), Alaska Outer Continental Shelf Region, 

Anchorage, Alaska, under Contract No. 1435-01-99-CT-30998, TO 10907, 

as part of the MMS Alaska Environmental Studies Program. 

May 2004 

The opinions, findings, conclusions, or recommendations expressed in this report 

or product are those of the authors and do not necessarily reflect the views of the 

U.S. Department of the Interior, not does mention of trade names or commercial 

products constitute endorsement or recommendation for use by the Federal 

Government.
iii

Table of Contents 

 Page

EXECUTIVE SUMMARY.................................................................... 1 

1.0 INTRODUCTION ....................................................................... 5 

2.0 METHODS ................................................................................ 7 

2.1 Sample Collection................................................................ 7 

2.1.1 Source Samples ...................................................... 7 

2.1.2 Offshore Water and Suspended Sediment Measurements 

during Open-Water Period ........................................ 7 

2.2 Laboratory Analyses: Inorganic Parameters and Organic Carbon ......... 7 

 2.2.1 Particulate and Dissolved Organic Carbon ...................... 7 

 2.2.2 Dissolved Metals, Major Ions, Chlorinity and Alkalinity ...... 8 

 2.2.3 Trace and Major Metals in Suspended Sediment ................ 9 

2.3 Quality Assurance and Quality Control for Inorganic Parameters and 

Organic Carbon ............................................................... 10 

2.3.1 Sample Tracking Procedure ....................................... 10 

2.3.2 Quality Control Measurements for Analysis ..................... 11 

2.3.3 Instrument Calibration ................................................ 11 

2.3.4 Matrix Spike Analysis ............................................... 11 

2.3.5 Duplicate Sample Analysis ........................................ 11 

2.3.6 Procedural Blank Analysis .......................................... 11 

2.3.7 CRM and SRM Analysis ............................................ 12 

2.4 Organic Analyses .................................................................. 14 

 2.4.1 Aqueous Sample Preparation ....................................... 14 

 2.4.2 Analysis for polynuclear Aromatic Hydrocarbons by Gas 

Chromatography/Mass Spectrometry .............................. 16 

2.4.3 Oil Spike Study Procedure .......................................... 16 

3.0 RESULTS AND DISCUSSION ........................................................ 18 

3.1 Source Rivers 2001 ................................................................ 18 

3.1.1 Transport of Water and Suspended Sediment ..................... 18 

3.1.2 Trends in Concentrations of Dissolved Major Ions ............... 23 

3.1.3 Interrelationships among Major Ions .............................. 27 

3.1.4 Reconstruction of Chemical Weathering to Produce Major 

 Ion Concentrations of Rivers ....................................... 29 

3.1.5 Dissolved Organic Carbon and Trace Metals ..................... 33 

3.1.6 Particulate Trace Metals and Organic Carbon .................... 38 

3.1.7 Major Elements in Suspended Solids .............................. 42 
iv

Table of Contents (continued) 

 Page

3.2 Source Rivers 2002 ............................................................... 44 

3.2.1 Overview and Transport of Water and Suspended Sediment ... 44 

3.2.2 Trends in Concentrations of Dissolved Major Ions ............... 48 

3.2.3 Dissolved Trace Metals and Dissolved Organic Carbon ......... 52 

3.2.4 Particulate Trace Metals and Organic Carbon ..................... 56 

3.3 Transport of Dissolved and Particulate Trace Metals and Organic 

Carbon by Rivers to the Coastal Beaufort Sea ........................... 58 

3.4 Partitioning of Metals between Dissolved and Particulate Phases in 

Rivers .......................................................................... 60 

3.5 Dissolved and Particulate Metals in the Coastal Beaufort Sea ............ 63 

3.6 Dissolved and Particulate Organic Substances in Seawater ............... 70 

3.7 Spike Study for Polycyclic Aromatic Hydrocarbons......................... 74 

4.0 SUMMARY AND CONCLUSIONS ................................................ 78 

5.0 REFERENCES .......................................................................... 80 

6.0 APPENDICES ........................................................................... 84 

Acknowledgements ..................................................................... 84 
v

List of Tables 

 Page

Section 2 

Table 2-1: Summary of instrumental methods and method detection limits 

for metal analysis of suspended sediment and water ................ 10 

Table 2-2: Data quality objectives and criteria ........................................ 12 

Table 2-3: Results for reference materials for dissolved metals ..................... 13 

Table 2-4: Target list of polynuclear aromatic hydrocarbons and alkyl 

polynuclear aromatic hydrocarbons................................ 15 

Table 2-5: Diagnostic ratios and parameters for polynuclear aromatic 

hydrocarbons ......................................................... 17 

Section 3 

Table 3-1: Locations of river sampling sites ............................................ 19 

Table 3-2: Conductivity and concentrations of total dissolved solids, calcium, 

magnesium, sodium, potassium, hydrogen ion, carbonate 

alkalinity, sulfate, chloride, fluoride, silicon and dissolved 

organic carbon in the Sagavanirktok, Kuparuk and Colville 

rivers during peak and off-peak discharge in June 2001 ....... 24 

Table 3-3: Varimax factor matrix of dissolved ions and dissolved organic carbon 

for the Sagavanirktok River ......................................... 28 

Table 3-4: Concentrations of total suspended solids, dissolved metals and 

dissolved organic carbon in the Sagavanirktok, Kuparuk and 

Colville rivers during peak and off-peak discharge in 

June 2001 .............................................................. 34 

Table 3-5: Pearson’s correlations between dissolved trace metals and dissolved 

organic carbon in the Sagavanirktok River during June 2001.. 36 

Table 3-6: Ranges and average concentrations of dissolved metals and dissolved 

organic carbon during August and September in rivers of the 

Alaskan and Russian Arctic ......................................... 37 

Table 3-7: Concentrations of particulate trace metals and particulate organic 

carbon in the Sagavanirktok, Kuparuk and Colville rivers 

during June 2001 ..................................................... 40 

Table 3-8: Correlations for particulate trace metals and particulate organic carbon in 

the Sagavanirktok River during June 2001 ......................... 40 

Table 3-9: Concentrations of particulate metals in the Sagavanirktok, Kuparuk and 

Colville rivers during June 2001 .................................... 42 

Table 3-10: Conductivity and concentrations of total dissolved solids, calcium, 

magnesium, sodium, potassium, hydrogen ion, carbonate 

alkalinity, sulfate, chloride, fluoride, silicon and dissolved 

organic carbon in the Sagavanirktok, Kuparuk rivers during 

peak discharge in June 2002 ........................................ 49 

Table 3-11: Concentrations of dissolved metals, dissolved organic carbon and total 

suspended solids in the Sagavanirktok, Kuparuk and Colville 

Rivers during peak discharge in 2002 and 2001 .................. 53 
vi

List of Tables (continued) 

 Page

Table 3-12: Concentrations of aluminum, barium, copper, iron, lead, zinc and 

particulate organic carbon in the Sagavanirktok and Kuparuk 

rivers during May-June 2002 ....................................... 56 

Table 3-13: Correlations for particulate trace metals and particulate organic 

carbon in the Sagavanirktok River during June 2002 ............ 57 

Table 3-14: Percentage of trace metals and organic carbon in the dissolved phase 

 during peak and off-peak discharge in the Sagavanirktok and 

 Kuparuk rivers ........................................................ 59 

Table 3-15: Means and standard deviations for salinity, total suspended solids 

 and concentrations of dissolved metals and dissolved organic 

 carbon for water collected from the coastal Beaufort Sea 

 during August 2000 .................................................. 64 

Table 3-16: Means and standard deviations for salinity, total suspended solids 

 and concentrations of dissolved metals and dissolved organic 

 carbon for water collected from the coastal Beaufort Sea 

 during August 2001 .................................................. 65 

Table 3-17: Means and standard deviations for salinity, total suspended solids 

 and concentrations of dissolved metals and dissolved organic 

 carbon for water collected from the coastal Beaufort Sea 

 during August 2002 .................................................. 66 

Table 3-18: Concentrations of selected dissolved metals in snow, Sagavanirktok 

River water and Beaufort Sea water compared with U.S. EPA 

 Criteria for freshwater and saltwater .............................. 67 

Table 3-19: Summary data for polycyclic aromatic hydrocarbons in Beaufort 

 Sea water samples ................................................... 71 

Table 3-20: Data summary for polycyclic aromatic hydrocarbons in Beaufort 

 Sea spike study ...................................................... 75 

 

 

 

 

 
vii

List of Figures 

 Page

Executive Summary 

Figure ES-1: Concentrations of dissolved and particulate organic carbon and dissolved and 

particulate iron in the Sagavanirktok River during June 2001 ........ 2

Figure ES-2: Concentrations of dissolved and particulate barium in the 

Sagavanirktok, Kuparuk and Colville rivers during summer 

2001 and log of the distribution coefficient for barium ......... 3 

Figure ES-3: Generalized distribution of dissolved arsenic and barium in source 

rivers and coastal water of the Beaufort Sea ....................... 3 

Section 1 

Figure 1-1: Map showing the western portion of the coastal Beaufort Sea 

with inset maps of Alaska, the oil production site at 

Northstar Island and a possible future drilling site 

at Liberty Prospect .................................................... 6 

Section 3 

Figure 3-1: Map showing locations of sampling sites in the Sagavanirktok, Kuparuk 

and Colville rivers with inset map showing study area ............ 19 

Figure 3-2: Water flow and concentrations of total suspended solids for the 

Sagavanirktok, Kuparuk and Colville rivers during 

June 2001 ............................................................... 21 

Figure 3-3: Sagavanirktok, Kuparuk and Colville rivers during June 2001 ................. 22 

Figure 3-4: (a) Conductivity and concentrations of dissolved (b) calcium, (c) magnesium, 

(d) carbonate alkalinity, (e) sulfate and (f) fluoride in the 

Sagavanirktok River and Kuparuk River during June 2001 ............ 25 

Figure 3-5: Concentrations of dissolved calcium plus magnesium versus carbonate 

alkalinity in the Sagavanirktok, Kuparuk and Colville rivers ......... 26 

Figure 3-6: Concentrations of dissolved (a) potassium and (b) hydrogen ion and pH 

in the Sagavanirktok and Kuparuk rivers, and dissolved organic 

carbon in the (c) Sagavanirktok River and (d) Kuparuk River 

during June 2001 .............................................................. 27 

Figure 3-7: Fraction of different rock types that were chemically weathered to produce 

the observed concentrations of dissolved major elements in the 

Sagavanirktok River during peak and off-peak flow in 2001 ........... 30 

Figure 3-8: Fraction of different rock types that were chemically weathered to 

produce the observed concentrations of dissolved major elements 

in the Kuparuk River during peak and off-peak flow in 2001 ........... 31 

Figure 3-9: Fraction of different rock types that were chemically weathered to produce 

the observed concentrations of dissolved major elements in the 

Colville River during peak and off-peak flow in 2001 .................... 32 

Figure 3-10: Concentrations of dissolved organic carbon and water discharge for the 

Sagavanirktok River during June 2001 and 2002 .......................... 33 
viii

List of Figures (continued) 

 Page

Figure 3-11: Concentrations of dissolved iron, copper, lead and zinc in the 

Sagavanirktok River during June 2001 ................................. 35 

Figure 3-12: Concentrations of dissolved barium in the Sagavanirktok River 

during June 2001 ....................................................... 38 

Figure 3-13: Concentrations of particulate barium, copper, iron, lead, zinc and particulate 

organic carbon in the Sagavanirktok River during June 2001 ......... 39 

Figure 3-14: Concentrations of particulate aluminum versus (a) barium and (b) iron for 

the Sagavanirktok, Kuparuk, and Colville rivers during 

June 2001 and 2002 .................................................... 41 

Figure 3-15: Concentrations of particulate aluminum versus (a) calcium, (b) magnesium, 

(c) sodium and (d) potassium for the Sagavanirktok, Kuparuk 

and Colville rivers during June 2001 ................................... 43 

Figure 3-16: Sagavanirktok, Kuparuk and Colville rivers during May-June 2002 ........... 45 

Figure 3-17: (a) Concentrations of total suspended solids and turbidity for the 

Sagavanirktok River during May-June 2002 and (b) Water discharge 

in the Sagavanirktok River for June 2002 ................................ 46 

Figure 3-18: Conductivity in the Sagavanirktok, Kuparuk and Colville rivers during 

May-June 2002 ........................................................... 47 

Figure 3-19: Water flow and concentrations of total suspended solids and turbidity for 

the Kuparuk River during May-June 2002 ............................ 47 

Figure 3-20: Water flow and concentrations of total suspended solids in the Colville 

River during May-June 2002 ............................................... 48 

Figure 3-21: Concentrations of dissolved calcium, magnesium and sulfate in the 

Sagavanirktok and Kuparuk rivers during June 2002 

and 2001 .................................................................. 50 

Figure 3-22: Concentrations of dissolved potassium in the Sagavanirktok and Kuparuk 

rivers during June 2002 ................................................. 51 

Figure 3-23: Concentrations of dissolved organic carbon in the Sagavanirktok and 

Kuparuk rivers during June 2002 ........................................ 51 

Figure 3-24: Concentrations of dissolved barium, cadmium, copper, iron, manganese 

and nickel in the Sagavanirktok and Kuparuk rivers 

during June 2002 .......................................................... 54 

Figure 3-25: Concentrations of dissolved lead and zinc in the Sagavanirktok 

and Kuparuk rivers during June 2002 .................................. 55 

Figure 3-26: Concentrations of dissolved organic carbon versus dissolved iron and potassium 

for the Sagavanirktok and Kuparuk rivers for June 2001 and 2002 .... 55 

Figure 3-27: Concentrations of barium for suspended sediment from the Sagavanirktok 

River for May-June 2002 .............................................. 57 

Figure 3-28: Average concentrations of dissolved and particulate barium and distribution 

coefficients in the Sagavanirktok, Kuparuk and Colville rivers ....... 61 

Figure 3-29: Concentrations of dissolved and particulate lead in the Sagavanirktok, 

Kuparuk and Colville Rivers during summer 2001 and log Kd 

for Pb .................................................................. 62 

 
ix

List of Figures (continued) 

 Page

Figure 3-30: Generalized distributions of dissolved arsenic in source rivers and coastal 

water of the Beaufort Sea ............................................ 67 

Figure 3-31: Concentrations of dissolved arsenic versus salinity ............................ 68

Figure 3-32: Generalized distributions of dissolved barium in source rivers and coastal 

water of the Beaufort Sea ........................................... 69 

Figure 3-33: Concentrations of dissolved barium versus salinity ........................... 69

Figure 3-34: Distribution histogram for polycyclic aromatic hydrocarbons in 

Beaufort Sea seawater samples – particulate fraction ................... 72 

Figure 3-35: Distribution histogram for polycyclic aromatic hydrocarbons in Beaufort 

Sea seawater samples – dissolved fraction ............................... 73 

Figure 3-36: Distribution histogram for polycyclic aromatic hydrocarbons in spiked sample 

 – particulate and dissolved fractions .................................... 76 

Figure 3-37: Distribution histogram for polycyclic aromatic hydrocarbons in spiking 

sediment and oil .......................................................... 77 

 

 
1

EXECUTIVE SUMMARY 

The Arctic Nearshore Impact Monitoring in the Development Area (ANIMIDA) Program 

was developed to monitor potential environmental changes related to oil and gas 

development in the Beaufort Sea with a special focus on the Northstar development. The 

ANIMIDA Program included a variety of biological and chemical studies. This report 

presents results from study of the partitioning of potential anthropogenic chemicals 

between dissolved and particulate phases in arctic rivers and the coastal water of the 

Beaufort Sea. 

 

In the dissolved form, trace metals and organic substances are generally more 

biologically available and have a greater chance to induce toxic effects in organisms. In 

general, concentrations of dissolved trace metals in coastal seawater are controlled by 

river runoff, adsorption on suspended sediment and biological uptake. During 2001 and 

2002, concentrations of dissolved metals were determined for the Sagavanirktok, 

Kuparuk and Colville rivers and for coastal water of the Beaufort Sea. The underlying 

theme in this effort was to understand the natural sources, transport pathways and 

concentrations of dissolved metals in the coastal Beaufort Sea. The natural processes that 

help regulate concentrations of dissolved substances must be understood before 

attempting to identify anthropogenic perturbations. 

Field activities for ANIMIDA Task 7 included sampling of rivers and offshore water 

during open-water periods of July-August 2000, 2001 and 2002 plus through-ice and 

river break-up efforts during May-June 2001 and 2002. Rivers are a major source of 

dissolved metals to the study area. The Sagavanirktok River was sampled daily during 

June 2001 and 2002 and the other two rivers were sampled every two to five days as 

logistics permitted. Samples of water and suspended sediment from the Sagavanirktok 

River also were collected at mile 401 on the Dalton Highway, and at the site of a gauging 

station maintained by the U.S. Geological Survey (U.S.G.S.), about 100 miles south of 

Deadhorse. 

Concentrations of the following dissolved and particulate metals: arsenic (As), barium 

(Ba), calcium (Ca), copper (Cu), iron (Fe), potassium (K), magnesium (Mg), manganese 

(Mn), sodium (Na), nickel (Ni), lead (Pb) and zinc (Zn), particulate aluminum (Al) and 

dissolved and particulate organic carbon (DOC and POC) were determined for the three 

rivers during June to August 2001 and 2002. Concentrations of dissolved trace metals 

were low, but different among the three rivers. For example, in the Sagavanirktok River, 

the following average concentrations of dissolved metals were determined: Pb at 15 ng/L, 

Cu at 0.6 μg/L and Ba at 32 μg/L whereas in the Colville River these three metals were 

found at concentrations of 60 ng/L, 2 μg/L and 50 μg/L, respectively. 

The most striking trend in the dissolved data was found for DOC with maximum levels of 

DOC in the Sagavanirktok River >8 mg/L during peak flow relative to 2 mg/L at lower 

flow (Figure ES-1). Concentrations of Fe, Mn, K and Cu followed trends for DOC quite 
2

05/28/01 06/04/01 06/11/01 06/18/01 06/25/01 07/02/01 DOC (mg/L)

0

2

4

6

8

10

POC (%)

0

1

2

3

4

5

0

100

200

300

400

500

05/28/01 06/04/01 06/11/01 06/18/01 06/25/01 07/02/01 Fe (%)

0

1

2

3

4

5

Fe (μg/L) 0

20

40

60

80

Figure ES-1. Concentrations of dissolved (triangles) and particulate (circles) organic carbon 

(DOC and POC) and dissolved (triangles) and particulate (circles) iron (Fe) in the 

Sagavanirktok River during June 2001. 

well (e.g., Fe in Figure ES-1). These trends are consistent with a pulse of exuded, DOCrich water from thawing soils in the drainage basin that occurred shortly after the initial 

melt event during the period of peak flow. Trends for dissolved Fe, Mn and K, also 

derived from thawing soils, matched the trend observed for DOC. Concentrations of 

dissolved Cu followed DOC relatively well; however, the magnitude of change was 

somewhat less than observed for the other elements. For dissolved Ba, Ni and Pb, 

concentrations shifted only slightly in response to the increase in levels of DOC. 

Concentrations of particulate metals (on the basis of μg metal/g suspended sediment) 

were rather uniform during June 2001 and fit metal/Al ratios defined for bottom sediment 

in the coastal Beaufort Sea. In most cases, very little (<10%) of the metal burden of the 

rivers was in the dissolved phase during the June period of high flow. 

The forms of the metals and controls on concentrations of dissolved metals in rivers are 

important to understanding subsequent behavior in the saline water of the coastal 

Beaufort Sea. Concentrations of dissolved and particulate Ba varied directly among the 

rivers (Figure ES-2) and thus a simple distribution coefficient (Kd) was used to explain 

observed concentrations, where 

(concentration of particulate metal in μg metal/g particles) 

Kd = _________________________________________________________________________ . 

 (concentration of dissolved metal in μg metal/g water) 

When this approach was used for Ba, the fit was quite good with the Kd for Ba averaging 

2.4 ± 0.5 x 104

 for all the rivers (Figure ES-2). This trend supports the concept that 

concentrations of Ba in suspended sediment regulate concentrations of dissolved Ba. The 

same approach also was applied to Pb and Cu; however, the fit was less consistent, 

suggesting that other factors, such as complexation with organic matter influences 

concentrations of dissolved Pb and Cu. 
3

 

Figure ES-2. Concentrations of dissolved and particulate barium (Ba) in the Sagavanirktok (Sag), 

Kuparuk (Kup) and Colville (Col) rivers during summer 2001 and log of the 

distribution coefficient (Kd) for Ba. Sag-g identifies upstream location at site of 

U.S.G.S. gauge. 

Concentrations of dissolved trace metals in the saline water of the coastal Beaufort Sea 

were generally lower than found in the rivers with the following observations: Pb at 4-7 

ng/L, Cu at 0.5 μg/L and Ba at 13 μg/L. Concentrations of total Hg in the coastal 

Beaufort Sea also were low at about 0.5-0.8 ng/L. Schematic representations for the 

distributions of dissolved As and Ba are shown in Figure ES-3. Concentrations of As 

increased from the rivers to the sea and concentrations of Ba decreased. 

Rivers

Coastal Beaufort Sea Coastal Beaufort Sea

0.1 μg/L

Dissolved As Dissolved As

0.9-1.3 μg/L @ Salinity ~ 30 psu

~0.4-0.7 μg/L 0.7 μg/L @ Salinity ~20 @ Salinity ~20 psu

~0.2-0.4 μg/L @ Salinity ~10 @ Salinity ~10 psu

 

Rivers

Coastal Beaufort Sea Coastal Beaufort Sea

30 μg/L 30 μg/L

Dissolved Dissolved Ba

~10 μg/L ~10 μg/L @ Salinity ~ 30 @ Salinity ~ 30 psu

30- 50 μg/L @ Salinity ~ 10 @ Salinity ~ 10 psu

 

Figure ES-3. Generalized distributions of dissolved arsenic (As) and barium (Ba) in source rivers 

and coastal water of the Beaufort Sea. 

The Total PAH (TPAH) concentrations in whole seawater samples (dissolved + 

particulate fractions) were low and ranged from 22 to 68 ng/L. The TPAH of the 

particulate fraction of the seawater samples ranged from 13.2 to 18.5 ng/L. The PAH 

distribution for the particles shows a petrogenic or petroleum hydrocarbon composition, 

characterized by a predominance of the 2- and 3-ringed alkyated PAH compounds, with a 

Sag Sag-g Kup Col

0

20

40

60

Dissolved Ba (μg/L)

31.7 ± 2.0

Sag Sag-g Kup Col

0

300

600

900

1200

Particulate Ba (μg/g)

Sag Sag-g Kup Col

0

1

2

3

4

5

log Kd for Ba
4

lower abundance of 4-, 5- and 6-ringed PAH. The PAH in the seawater samples were 

primarily associated with suspended sediment. The composition of the PAH in the 

suspended sediment was similar to that observed for riverine and benthic sediment in the 

ANIMIDA study area. Analysis of the dissolved fraction showed no detectable PAH in 

the dissolved phase in support of the statement that the PAH are bound to suspended 

sediment and do not partition to any great extent into the dissolved phase. 

The main conclusions from ANIMIDA Task 7 are as follows: (1) concentrations of 

dissolved trace metals and PAH in the study area are very low and characteristic of 

pristine water, (2) concentrations of some metals can be modeled with a simple 

distribution coefficient, and (3) active physical, chemical and biological processes are at 

work to create a dynamic, yet predictable, distribution of dissolved trace metals in the 

study area. Such information will be useful for long-term monitoring (years, decades and 

centuries) and will provide an evolving capability for predicting impacts from any spills 

or other releases of chemicals within the drainage basin or the coastal sea. 
5

1.0 INTRODUCTION 

The Arctic Nearshore Impact Monitoring in the Development Area (ANIMIDA) Program 

was developed to monitor potential environmental changes related to oil and gas 

development in the Beaufort Sea with a special focus on the Northstar development. This 

report presents results from study of partitioning of potential anthropogenic chemicals 

between dissolved and particulate phases. The study was designed to determine 

concentrations of dissolved chemicals in the coastal Beaufort Sea and identify the degree 

of partitioning with suspended sediment. Samples of water and suspended sediment were 

collected from three area rivers and a segment of the coastal Beaufort Sea that 

encompassed Northstar Island and the Liberty Prospect (Figure 1-1). 

Concentrations of dissolved and particulate substances in the water column are sensitive 

indicators of low levels of environmental contamination in a coastal setting. Because of 

the transient nature of some dissolved constituents, along with difficulties in collection 

and analysis of samples, potential anthropogenic chemicals are usually monitored by 

analyzing sediment and biota. However, at this point in the evolution of environmental 

research in the coastal Beaufort Sea, study of dissolved and particulate phases for 

potential anthropogenic chemicals seemed warranted. In the dissolved form, trace metals 

and organic substances are generally more biologically available and have a greater 

chance to induce toxic effects in organisms. Most spills in coastal areas, whether an oil, 

aqueous or solid discharge, will first impact the water column. A dependable capability 

for predicting the behavior of potential anthropogenic chemicals under various discharge 

or sediment resuspension scenarios is needed. Furthermore, no reliable, consistent data 

set for dissolved trace substances is presently available for the coastal Beaufort Sea. 

The case for studying dissolved and particulate phases of potential anthropogenic 

chemicals in the Beaufort Sea is enhanced by the relatively uniform composition of 

suspended sediment in area water. If partitioning between dissolved and particulate 

phases can be predicted, then the response of the system to addition of any anthropogenic 

chemical also may be predicted. Do dissolved trace substances stay in solution or are 

they adsorbed on suspended particles? In addition to addressing these issues, a solid 

database for dissolved constituents has been produced to provide a potentially valuable 

marker for long-term changes in the system that does not presently exist. 

The overall objectives for ANIMIDA Task 7 were as follows: 

1. To determine concentrations of selected metals and organic substances in dissolved 

and particulate forms in water of the source rivers and the coastal Beaufort Sea. 

2. To determine partitioning coefficients (particulate/dissolved) for selected metals and 

organic substances. 

3. To determine the partitioning between dissolved and particulate phases for 

polynuclear aromatic hydrocarbons (PAH) in North Slope crude oil from a laboratory 

spiking experiment using Beaufort Sea water. 
6

Figure 1-1. Map showing the western portion of the coastal Beaufort Sea with inset maps of 

Alaska, the oil production site at Northstar Island and a possible future drilling site 

at Liberty Prospect. The ANIMIDA study focused mainly on the area shown in the 

shaded box. 

The underlying theme in this effort is to understand the natural sources, transport 

pathways and concentrations of dissolved substances in the coastal Beaufort Sea. The 

natural processes and variations in concentrations of dissolved substances must be 

understood before attempting to identify anthropogenic perturbations. 

Field activities for ANIMIDA Task 7 included sampling offshore water and rivers during 

open-water periods of July-August 2000, 2001 and 2002 plus through-ice and river 

break-up efforts during May-June 2001 and 2002. The strong ties between ANIMIDA 

Tasks 5 and 7 lead to some overlap in reporting. The Results and Discussion section for 

ANIMIDA Task 7 will not restate the details of work reported in Trefry et al. (2004). 

Instead, the focus here will be on concentrations and mechanisms that control dissolved 

substances in the source rivers and offshore water of the coastal Beaufort Sea. 

Study Area 

P1 

.

 

. E1
7

2.0 METHODS 

2.1 Sample Collection 

2.1.1 Source Samples 

Water samples were collected from the Sagavanirktok, Colville and Kuparuk rivers in 1-

L, acid-washed, low-density, polyethylene (LDPE) bottles. Some samples were obtained 

by wading into the river, waiting until any disturbed sediment was washed down stream, 

and then opening an acid-washed 1- or 2-L, LDPE bottle below the surface of the water. 

When the bottle was full, it was sealed beneath the surface, retrieved, placed in a plastic 

bag, labeled and stored in a cooler for return to the on-site laboratory facilities to be 

filtered. During May-June 2001 and 2002, samples from the Sagavanirktok and Kuparuk 

rivers were collected by a special water sampler that held acid-washed LDPE bottles and 

could be lowered from bridges across the river. 

 

2.1.2 Offshore Water and Suspended Sediment Measurements during OpenWater Period 

Seawater samples were collected from the bow of a small rubber boat while rowing 

upstream or upwind. An acid-washed 1- or 2-L LDPE bottle was opened at about 10 cm 

below the surface of the water. When the bottle was full, it was sealed beneath the 

surface, retrieved, and placed in a plastic bag for storage. In the on-site laboratory, the 

water samples were vacuum filtered through polycarbonate filters (Poretics, 47-mm 

diameter, 0.4-μm pore size). Prior to the field effort, the filters were acid washed in 5N 

HNO3, rinsed three times with distilled, deionized water (DDW), dried and then weighed 

to the nearest μg using a Sartorius Model M3P electronic balance under cleanroom 

conditions. Vacuum filtration at an on site laboratory was carried out in a Class-100 

laminar-flow hood using acid-washed glassware. The filtered water was acidified with 1 

mL of ULTREX HNO3 per liter of water and stored in a separate, acid-washed LDPE 

bottle. Particle-bearing filters were sealed in acid-washed petri dishes, labeled, doublebagged in plastic bags and then stored until dried and re-weighed in the Marine & 

Environmental Chemistry Laboratories at Florida Institute of Technology (FIT). 

2.2 Laboratory Analyses: Inorganic Parameters and Organic Carbon 

2.2.1 Particulate and Dissolved Organic Carbon 

Samples for particulate organic carbon (POC) and dissolved organic carbon (DOC) were 

prepared by filtration of seawater and river water through pre-combusted Gelman Type 

A/E glass fiber filters mounted on acid-washed filtration glassware within a Class-100 

laminar-flow hood. The POC filters were sealed in acid-washed petri dishes, labeled, 

double bagged in plastic and then stored frozen until dried at FIT. The dissolved samples 

saved for DOC were placed in acid-washed glass vials with Teflon-lined caps, labeled, 

and frozen until analysis at FIT. 
8

At FIT, the POC filters were treated with H3PO4 to remove inorganic carbon phases, 

rinsed with DDW, dried and their particulate mass determined. The filters were then 

placed in ceramic boats and combusted at 900°C in a Shimadzu TOC-5050A carbon 

system with SSM-5000A solid sampling module following the manufacturer’s 

instructions. The POC content of the samples was determined using a four-point 

calibration curve with pure sucrose as the standard. The calibration curve was checked 

every 10 samples by analyzing the certified reference material (CRM) MESS-2, a marine 

sediment issued by the National Research Council of Canada (NRC). 

The DOC concentrations of the seawater and river water samples were calculated by 

difference, total carbon (TC) minus inorganic carbon (IC) as determined by combustion 

in the Shimadzu TOC-5050A system. Four-point calibration curves were prepared 

using potassium hydrogen phthalate (TC) and sodium bicarbonate (IC). The calibration 

curve was checked every 10 samples by repeat analysis of a mid-range standard. 

2.2.2 Dissolved Metals, Major Ions, Chlorinity and Alkalinity 

The seawater concentrations of dissolved As, Cd, Cr, Cu, Pb and Zn were determined on 

extracts obtained using a reductive precipitation procedure derived from Nakashima et al. 

(1988). In this procedure, ultra-high purity Pd, Fe and NaBH4 are used to precipitate the 

metals that are then collected by filtration and redissolved in ultra-high purity HNO3 and 

HCl. This procedure was carried out using 400-mL aliquots of seawater and a seawater 

CRM (CASS-3 issued by the NRC) with a final extract volumes of ~4 mL, resulting in a 

~100-fold concentration of the seawater metals prior to analysis. The extracts were 

transferred to acid-washed 7.5-mL LDPE bottles, sealed, labeled and then stored in a 

plastic bag until analysis. Concentrations of dissolved Ba were determined directly on 

diluted aliquots of the seawater samples. River water samples were analyzed directly for 

Ba, Ca, Cu, Fe, K, Mg, Mn, Na and Ni as described below. Concentrations of Pb and Zn 

in river water were determined by reductive precipitation of 400-mL aliquots of the 

samples and the river water CRM SLRS-3 (issued by the NRC). Labware used in the 

extraction procedure and subsequent analysis was acid-washed with hot HNO3 and rinsed 

three times with reagent water prior to use. 

Total dissolved Hg levels in seawater and river water were determined on separate 

portions that had been treated with bromine monochloride solution (Szakacs et al., 1980) 

to oxidize organic ligands and preserve the samples until analysis. 

The metal concentrations of the river water, river water extracts, CRMs and blanks were 

determined by flame atomic absorption spectrometry (FAAS), graphite furnace atomic 

absorption spectrometry (GFAAS), inductively coupled plasma-mass spectrometry (ICPMS) or cold-vapor atomic fluorescence spectrometry (CVAFS) (Table 2-1). 

Concentrations of Ca, K, Mg and Na in river water were measured directly by FAAS -

using a Perkin-Elmer Model 4000 AAS. Concentrations of dissolved As in the extracts 

were determined by GFAAS with a Perkin-Elmer Model 5100PC AAS equipped with 

an HGA-600 graphite furnace and AS-60 autosampler. Dissolved Pb and Zn 

concentrations of the river water extracts were quantified by ICP-MS using a Perkin-
9

Elmer ELAN 5000 instrument. Dissolved Cu, Fe and Mn concentrations were 

measured directly for river water using a Perkin-Elmer Model 4000 AAS equipped with 

an HGA-400 graphite furnace and AS-40 autosampler. Dissolved Ba and Ni 

concentrations were determined directly on the river water samples by ICP-MS using a 

Perkin-Elmer ELAN 5000 instrument. Mercury in water samples was preconcentrated 

by gold amalgamation followed by analysis with CVAFS using a Brooks-Rand Model 

III Mercury System. 

The metal concentrations of the seawater, seawater extracts, CRMs and blanks were 

determined by GFAAS, ICP-MS or CVAFS (Table 2-1). Concentrations of dissolved Cr 

and Cu in the extracts were determined by GFAAS using a Perkin-Elmer Model 4000 

AAS with an HGA-400 graphite furnace and AS-40 autosampler. The As concentrations 

of the seawater extracts were determining using a Perkin-Elmer Model 5100PC AAS 

with an HGA-600 graphite furnace and AS-60 autosampler. Dissolved Cd, Pb and Zn 

concentrations of the seawater extracts were quantified by ICP-MS using a PerkinElmer ELAN 5000 instrument. Dissolved Ba concentrations were measured directly on 

the seawater samples by ICP-MS using a Perkin-Elmer ELAN 5000 instrument and 

multiple-spike Method of Standard Additions. Total dissolved Hg concentrations were 

determined by CVAFS using a Brooks-Rand Model III Mercury System following 

preconcentration by gold amalgamation. 

River water chlorinity (Cl-), sulfate (SO4

2-) and fluoride (F-

) concentrations were 

determined by ion chromatography using a Dionex DX-600 ion chromatograph (IC). 

Standard curves were prepared utilizing a Dionex Five Anion Standard certified 

solution. The IC column was a Dionex IonPac AS9-HC and the eluent was 9mM 

NaHCO3. Alkalinity was determined by titration using the method of Strickland and 

Parsons (1972). 

2.2.3 Trace and Major Metals in Suspended Sediment 

Filters bearing suspended sediment and milligram quantities of standard reference 

material (SRM) #2704, a river sediment SRM issued by the National Institute of 

Standards and Technology (NIST), were digested in stoppered, 15-mL Teflon test tubes 

using Ultrex II HNO3, HF and HCl. The sealed tubes were placed in an 80°C water 

bath where refluxing of the acids completely dissolved the particles on the filters. After 

digestion, the resultant solutions were transferred to acid-washed, 15-mL polyethylene 

bottles, diluted to ~6 mL with DDW rinses of the Teflon tubes and stored in a plastic 

bag until analyzed. 

Metal concentrations for the digested particulate samples, SRMs and blanks were 

determined by FAAS, GFAAS or ICP-MS in a manner compatible with EPA Series 

7000, 6010A and 7470 (USEPA, 1993), respectively. Concentrations of particulate Al, 

Fe and Zn were determined by FAAS using a Perkin-Elmer Model 4000 AAS. 

Concentrations of Cr and Cu were determined by GFAAS using a Perkin-Elmer Model 

4000 AAS equipped with an HGA-400 graphite furnace and AS-40 autosampler. 
10

Concentrations of As were quantified by GFAAS using a Perkin-Elmer model 5100 

instrument equipped with an HGA-600 graphite furnace and an AS-60 autosampler. 

Values for Ba, Cd and Pb were determined by ICP-MS using a Perkin-Elmer ELAN 

5000 instrument. In all cases, the instrument manufacturers’ specifications were 

followed and adherence to QA/QC requirements was maintained. 

Table 2-1. Summary of instrumental methods and method detection limits (MDL) for metal 

analysis of suspended sediment (dry weight basis) and water. 

Suspended Sediment Water 

Metal Method MDLs 

(μg metal/g, 

dry weight) 

Method MDLs 

(μg metal/L) 

Al – aluminum FAAS 1500 - - 

As – arsenic GFAAS 1.8 GFAAS 0.00811 

Ba – barium ICP-MS 9 ICP-MS 0.1 

Ca – calcium FAAS 230 FAAS 0.01 mg/L 

Cd – cadmium ICP-MS 0.03 ICP-MS 0.0001 

Cr – chromium FAAS 0.33 GFAAS 0.005 

Cu – copper FAAS 0.4 GFAAS 0.003 

Fe – iron FAAS 250 GFAAS 0.01 

K – potassium FAAS 250 FAAS 0.02 mg/L 

Hg – mercury - - CVAFS 0.03 ng/L 

Mg – magnesium FAAS 40 FAAS 0.01 mg/L 

Mn – manganese FAAS 170 GFAAS 0.1 

Na – sodium FAAS 0.7 FAAS 0.008 mg/L 

Ni – nickel ICP-MS 0.2 ICP-MS 0.02 

Pb – lead ICP-MS 82 ICP-MS 0.002 

Zn – zinc FAAS 2 ICP-MS 0.01 

POC/DOC Shimadzu

Carbon System 

0.01% Shimadzu

Carbon System

0.1 mg/L 

Notes: CVAFS = Cold Vapor Atomic Fluorescence Spectrometry 

FAAS = Flame Atomic Absorption Spectrometry 

GFAAS = Graphite Furnace Atomic Absorption Spectrometry 

ICP-MS = Inductively Coupled Plasma-Mass Spectrometry 

MDL = Method Detection Limit 

2.3 Quality Assurance and Quality Control for Inorganic Parameters and Organic 

Carbon

2.3.1 Sample Tracking Procedure 

All sediment samples were collected by, transported by and stored by personnel from 

FIT. Upon return-to or arrival at the laboratory, each sample was carefully inspected to 

insure that it was intact and that the identification number was clearly readable. All 

samples for organic carbon were kept frozen (-20°C) until processed for analysis. 
11

2.3.2 Quality Control Measurements for Analysis 

For this project, QC measures included balance calibration, instrument calibration 

(FAAS, GFAAS, CVAAS, ICP-MS, TOC analyzer, and in-situ instrument sensors), 

matrix spike analysis for each metal, duplicate sample analysis, analysis of CRMs and 

SRMs, procedural blank analysis and standard checks. With each batch of up to 20 

samples, two procedural blanks, two CRMs or SRMs, two duplicate samples and two 

matrix-spiked samples were analyzed. Data quality objectives (DQOs) for these quality 

control measurements are provided in Table 2-2. 

2.3.3 Instrument Calibration 

Electronic balances used for weighing samples and reagents were calibrated prior to each 

use with certified NIST-traceable standard weights. All pipets (electronic or manual) 

were calibrated prior to use. Each of the spectrometers used for metal analysis was 

initially standardized using a three- to five-point calibration with a linear correlation 

coefficient of r ≥ 0.999 required before experimental samples could be analyzed. 

Analysis of complete three- to five-point calibrations and/or single standard checks 

alternated every 5-10 samples until all the analyses were complete. The relative standard 

deviation (RSD) between complete calibration and standard checks was required to be 

<15% or recalibration and reanalysis of the affected samples were performed. 

2.3.4 Matrix Spike Analysis 

Matrix spikes were prepared for a minimum of 5% of the total number of samples 

analyzed and included each metal to be determined. Results from matrix spike analysis 

using the method of standard additions provide information on the extent of any signal 

suppression or enhancement due to the sample matrix. If necessary (i.e., spike results 

outside 80-120% limit), spiking frequency was increased to 20% and a correction was 

applied to the metal concentrations of the experimental samples. 

2.3.5 Duplicate Sample Analysis 

Duplicate samples from homogenized field samples (as distinct from field replicates) 

were prepared in the laboratory for a minimum of 5% of the total samples. These 

laboratory duplicates were included as part of each set of sample digestions and analyses 

and provide a measure of analytical precision. 

 

2.3.6 Procedural Blank Analysis 

Two procedural blanks were prepared with each set of 20 samples to monitor potential 

contamination resulting from laboratory reagents, glassware and processing procedures. 

These blanks were processed using the same analytical scheme, reagents and handling 

techniques as used for the experimental samples. 
12

2.3.7 CRM and SRM analysis 

A common method used to evaluate the accuracy of environmental data is to analyze 

reference materials, samples for which consensus or "accepted" analyte concentrations 

exist. The following CRMs and SRMs were used to check accuracy for dissolved metals: 

nearshore seawater CASS-3 (NRC), river water SLRS-3 and SLRS-4 (NRC) and natural 

water #1640 (NIST). Milligram quantities of the following CRMs and SRMs were used 

to assess accuracy for suspended sediment: marine sediment CRM MESS-2 (NRC) and 

Buffalo River sediment SRM#2704 (NIST). Metal concentrations obtained for the 

reference materials were required to be within 20% of accepted values for >85% of other 

certified analyses. Results for dissolved metals are listed in Table 2-3; results for 

suspended sediment are presented in Trefry et al. 2004. Data for QA/QC measurements 

for each cruise are given with the complete data sets in Appendices A, B and C. 

Table 2-2. Data quality objectives and criteria. 

Element or Sample Type 

Criteria 

Minimum Frequency Data Quality 

Objective/Acceptance 

Initial Calibration Prior to every batch of samples 

Standard Curve 

3-5 point curve depending 

on the element and a blank 

Correlation coefficient r ≥

0.999 for all analytes 

Continuing Calibration Must end every analytical 

sequence; for flame, repeat 

all standards every 5 samples; 

for graphite furnace and ICPMS, recheck standard 

 after every 8-10 samples 

%RSD <15% for all 

analytes 

Certified and Standard 

Reference Materials 

Two per batch of 20 samples Values must be within 20% 

of accepted values for 

>85% of the certified 

analytes and within 25% for 

Hg 

Method Blank Two per batch of 20 samples No more than 2 analytes to 

exceed 5x MDL 

Matrix Spike and 

Spike Method Blank 

Two per batch of 20 samples 80-120% 

Lab Duplicate Two per batch of 20 samples RSD <25% for 65% of 

analytes 
13

Table 2-3. Results for reference materials for dissolved metals. 

a

 ± 95 confidence limits. 

b

 ± 1 standard deviation. 

c

 Reference Value (provided by NIST, not certified). 

Standard (SRM) or Certified 

(CRM) Reference Material 

Certified Concentrationsa 

(μg/L) 

This Studyb 

(μg/L) 

CRM CASS-3 (NRC) 

As (n = 8) 1.09 ± 0.07 1.06 ± 0.04 

Ba (n = 2) - 8.9 ± 0.4 

Cd (n = 7) 0.030 ± 0.005 0.027 ± 0.001 

Cr (n = 6) 0.092 ± 0.006 0.092 ± 0.001 

Cu (n = 6) 0.517 ± 0.062 0.538 ± 0.016 

Pb (n = 7) 0.012 ± 0.004 0.012 ± 0.002 

Zn (n = 7) 1.24 ± 0.25 1.11 ± 0.08 

 

CRM SLRS-3 (NRC) 

Ba (n = 6) 13.4 ± 0.2 13.6 ± 0.2 

Ca (n = 5) 6.0 ± 0.4 mg/L 6.1 ± 0.2 mg/L 

Fe (n = 5) 100 ± 2 101 ± 2 

K (n = 5) 0.7 ± 0.1 mg/L 0.7 ± 0.1 mg/L 

Mg (n = 5) 1.6 ± 0.6 mg/L 1.6 ± 0.1 mg/L 

Mn (n = 5) 3.9 ± 0.3 3.8 ± 0.2 

Na (n = 5) 2.3 ± 0.2 mg/L 2.3 ± 0.1 

Pb (n = 5) 0.086 ± 0.007 0.084 ± 0.004 

Zn (n = 5) 1.04 ± 0.09 1.05 ± 0.04 

 

CRM SLRS-4 (NRC) 

Cu (n = 2) 1.81 ± 0.08 1.82 ± 0.04 

Pb (n = 3) 0.086 ± 0.007 0.086 ± 0.002 

Zn (n = 3) 0.93 ± 0.10 0.89 ± 0.03 

 

SRM #1640 (NIST) 

Ba (n = 6) 148.0 ± 2.2 147.5 ± 2.0 

Cu (n = 5) 85.2 ± 1.2c 84.9 ± 1.8 

Ni (n = 5) 27.4 ± 0.8c 27.7 ± 0.7 

 
14

2.4 Organic Analyses 

During the 2001 summer field season, eight large volume (4 L) samples of Beaufort Sea 

water were collected for PAH analyses. Three samples were collected at sites near 

Northstar Island, three were collected at Beaufort Sea Monitoring Program (BSMP) 

stations, and two were collected at stations near Liberty Prospect. Eight replicate 

samples were collected at station 3A (Figure 1-1). One of the station 3A replicates was 

analyzed with the other Beaufort Sea seawater samples. The remaining seven replicates 

were used in a spiking study to assess partitioning of potential organic contaminants 

between the dissolved and particulate phases. 

Analysis for organic contaminants was conducted by ADL/ICF’s environmental 

chemistry laboratory1

. The analyses were conducted in accordance with the laboratory’s 

standard operating procedures (SOPs) and generally followed the same procedures used 

in previous BSMP studies (Boehm et al., 1990). The aqueous samples were analyzed for 

PAH by gas chromatography with detection by mass spectrometry (GC/MS). Targeted 

compounds are listed in Table 2-4. This section describes the analytical methods that 

were used to perform the organic chemical analyses. 

2.4.1 Aqueous Sample Preparation 

The 4-L aqueous samples were filtered through pre-combusted glass fiber filters to isolate 

the dissolved and particulate phases. The filtered water and filtrate samples were 

refrigerated until sample preparation and were extracted within 7 days of preparation to 

meet holding time requirements. The filter samples were prepared using a procedure 

based on United States Environmental Protection Agency (USEPA) Method 3550A, 

Ultrasonic Extraction (USEPA, 1993). The method modifications included orbital 

shaking of the sample in extraction solvent for 1 hour following the final sonication to 

enhance recovery of target contaminants. The filtered water samples were prepared using 

a procedure based on USEPA Method 3510C, Separatory Funnel Liquid-Liquid 

Extraction. A volume of approximately 4 L was extracted for each sample. Surrogate 

compounds were spiked into the samples after the first addition of solvent and before the 

first extraction. All samples were spiked with “low-level” surrogates (as defined by the 

laboratory SOP) because target compound concentrations in the samples were expected 

to be at trace levels. A procedural blank, blank spike, and blank spike duplicate were 

prepared and analyzed with each sample extraction batch. Clean filters were used for the 

procedural blank and blank spikes associated with the filter samples. 

 

1

 During the course of this program, the prime contractor Arthur D. Little (ADL) filed for bankruptcy protection and was subsequently 

sold off by division. The environmental consulting and laboratory division of ADL was purchased by ICF Consulting in May 2002. 

To avoid confusion and remain consistent, the laboratory will be referred to throughout this report as the ADL/ICF laboratory. The 

ADL/ICF laboratory performed organic analysis on dissolved and particulate samples for the ANIMIDA program under Task Order 7. 

The ADL standard operating procedures (SOPs) were adopted, as is, with no technical changes by ICF. In March 2003, ICF closed 

the environmental laboratory located in Cambridge, MA. Fortunately, all necessary samples analyses for this program were 

completed prior to the close of the laboratory. Copies of all SOPs and the hard-copies and electronic instrument files for the organic 

chemistry data are archived at the ICF Consulting office in Lexington, MA. 
15

Table 2-4. Target list of polynuclear aromatic hydrocarbons and alkyl polynuclear aromatic 

hydrocarbons. 

Compound Reporting 

Code 

Internal 

Standard/

Surrogate 

Reference 

Compound Reporting 

Code 

Internal 

Standard/

Surrogate 

Reference 

Naphthalene C0N A/1 Benzo[a]anthracene BAA B/3 

C1-Naphthalenes C1N A/2 

C2-Naphthalenes C2N A/2 Chrysene C0C B/3 

C3-Naphthalenes C3N A/2 C1-Chrysenes C1C B/3 

C4-Naphthalenes C4N A/2 C2-Chrysenes C2C B/3 

 C3-Chrysenes C3C B/3 

Acenaphthylene ACEY A/2 C4-Chrysenes C4C B/3 

Acenaphthene ACE A/2 

Biphenyl BIP A/2 

 Benzo[b]fluoranthene BBF B/4 

Fluorene C0F A/2 Benzo[k]fluoranthene BKF B/4 

C1-Fluorenes C1F A/2 Benzo[e]pyrene BEP B/4 

C2-Fluorenes C2F A/2 Benzo[a]pyrene BAP B/4 

C3-Fluorenes C3F A/2 Perylene PER B/4 

 Indeno[1,2,3-

c,d]pyrene 

IND B/4 

Anthracene C0A A/3 Dibenzo[a,h]anthrace

ne 

DAH B/4 

Phenanthrene C0P A/3 Benzo[g,h,i]perylene BGP B/4 

C1-

Phenanthrenes/Anthracenes 

C1P/A A/3 

C2-

Phenanthrenes/Anthracenes 

C2P/A A/3 

C3-

Phenanthrenes/Anthracenes 

C3P/A A/3 

C4-

Phenanthrenes/Anthracenes 

C4P/A A/3 

 

Dibenzothiophene C0D A/3 

C1-Dibenzothiophenes C1D A/3 Surrogate Compounds 

C2-Dibenzothiophenes C2D A/3 Naphthalene-d8 D8N A/1 

C3-Dibenzothiophenes C3D A/3 Acenaphthene-d10 D10ACE A/2 

 Phenanthrene-d10 D10PH A/3 

Fluoranthene FLANT A/3 Benzo(a)pyrene-d12 D12BAP B/4 

Pyrene PYR A/3 

C1-Fluoranthenes/Pyrenes C1F/P A/3 Internal Standard 

C2-Fluoranthenes/Pyrenes C2F/P A/3 Fluorene-d10 D10F A 

C3-Fluoranthenes/Pyrenes C3F/P A/3 Chrysene-d12 D12C B 

Internal Standard/Surrogate Reference indicates internal standard used for quantitation and surrogate 

compound used to correct analytical results. 

2-ring PAHs include: napthalenes, acenaphthylene, acenaphthene, biphenyl, and fluorenes. 

3-ring PAHs include: anthracenes, phenanthrenes, and dibenzothiophenes. 

4-ring PAHs include: fluoranthenes, pyrenes, benzo(a)anthracene, chrysenes, benzo(b)fluoranthene, and 

benzo(k)fluoranthene. 

5-ring PAHs include: benzo(e)pyrene, benzo(a)pyrene, perylene, indeno(1,2,3-cd)pyrene, and 

dibenz(a,h)anthracene Benzo(g,h,i)perylene is a 6-ring PAH. 
16

After solvent extraction, samples were concentrated using a Kuderna-Danish concentrator 

on a hot water bath. The extracts were reduced to a measured final volume under a 

stream of nitrogen. The final sample extracts were spiked with PAH internal standards, 

as appropriate for each extract. In general, the extracts were concentrated to 

approximately 250 μL before adding the internal standards to lower detection limits. 

2.4.2 Analysis for Polynuclear Aromatic Hydrocarbons by Gas 

Chromatography/Mass Spectrometry 

Analysis for PAHs was performed using a method based on USEPA Method 8270 

(USEPA, 1993). The method modifications include analysis for an expanded list of PAH 

(Table 2-4) and operation in the selected ion monitoring mode to lower detection limits. 

The sample extract was injected onto a 30-m long by 0.25-mm ID fused-silica capillary 

column with DB-5 bonded phase. This column provided baseline resolution of target 

PAHs. The injection port is designed for splitless injection and includes a silanized widebore glass liner containing a plug of silanized glass wool to reduce high-molecularweight mass discrimination. 

Qualitative identification of target compounds was made by comparison to a standard 

mixture of target PAHs. Identification of alkyl PAHs was made by comparison to 

reference oil samples analyzed with each batch of samples. The concentrations of the 

individual PAHs were calculated relative to one of the two internal standards that were 

spiked into the sample just prior to instrumental analysis. The target PAH concentrations 

were quantified using average response factors (RFs) generated from the five-point 

calibration curve. To quantify the alkyl PAH, homologue groups were assigned the RF 

of their respective parent PAH compound. Compound concentrations were corrected 

based on surrogate recoveries. A variety of diagnostic ratios and parameters are used for 

data interpretation (Table 2-5). 

2.4.3 Oil Spike Study Procedure 

Approximately 640 mg of wet (360 mg dry) homogenized Beaufort Sea sediment from 

sample 00-N23-01-PHC were added to each of the seven replicate 4-L water samples 

collected at station 3A. Sample 00-N23-01-PHC was selected for spiking because it was 

mostly fine-grained sediment (98.6% silt + clay) and had a representative Total PAH 

concentration of 540 μg/Kg. Assuming all of the fine-grained sediment became 

suspended in addition to the original total suspended solids (TSS) concentration for 

sample 3A, the final TSS for the spiked samples was 95 mg/L. Each sample also was 

spiked with ~200 mg of North Slope crude oil. The North Slope Crude oil was a Valdez 

Terminal composite crude oil collected in March 1989. A sediment blank was generated 

by adding ~640 mg of wet homogenized Beaufort Sea sediment to 4 L of 

distilled/deionized water. Clean magnetic stir bars were added to each sample jar. The 

samples were stirred for 24 hours at ~100 rpm in a walk-in refrigerator, held at 4°C +

2°C. Approximately 3 L of the sample were removed from the sample jars by placing a 

clean Teflon tube into the sample. The end of the Teflon tube was covered with a 
17

small piece of clean aluminum foil to prevent the uptake of any potential oil sheen while 

passing through the surface of the water. The samples were siphoned from near the 

bottom of the sample jar while the stir bar was spinning. The samples were then filtered 

through pre-combusted glass fiber filters to isolate the dissolved and particulate phases. 

The filtered water and filter samples were refrigerated until sample preparation and were 

extracted within 7 days of preparation to meet holding time requirements. To avoid loss 

of the lower molecular weight PAHs, the filter samples were not dried and weighed after 

filtering to determine the suspended sediment mass collected on the filter. 

Table 2-5. Diagnostic ratios and parameters for polynuclear aromatic hydrocarbons. 

Parameter Relevance in Environmental Samples 

N/P The naphthalenes (N) to phenanthrenes/anthracenes (P) ratio is diagnostic for inputs of 

fresh petroleum, and as a weathering indicator. Naphthalenes are characteristic of fresh 

crude oil; the ratio decreases with increased weathering. (N= Naphthalene series [C0N + 

C1N + C2N + C3N + C4N]; P= Phenanthrene/Anthracene Series [C0P/A + C1P/A + 

C2P/A + C3P/A + C4P/A]). 

Perylene A biogenic PAH formed during the early diagenesis in marine and lacustrine sediment; 

may be associated with terrestrial plant source precursors. 

Total PAH The sum of all PAH target analytes; includes 2- through 6-ring parent PAH and C1 - C4 

alkyl-substituted PAH. 

2-Ring PAH The sum of PAH compounds with 2 rings (napthalenes, acenaphthylene, acenaphthene, 

biphenyl, and fluorenes ). 

3-Ring PAH The sum of PAH compounds with 3 rings (anthracenes, phenanthrenes, and 

dibenzothiophenes). 

4-Ring PAH The sum of PAH compounds with 4 rings (fluoranthene, pyrene, chrysene, 

benzo[a]anthracene, benzo[b]fluoranthene, and benzo[k]fluoranthene). 

5+

-Ring PAH The sum of PAH compounds with 5 or 6 rings (benzo[a]pyrene, dibenz[a,h]anthracene, 

benzo[g,h,i]perylene, and indeno[1,2,3,-c,d]pyrene). 

Pyrogenic PAH The sum of combustion PAH compounds (4-, 5-, and 6-ring PAH: fluoranthene, pyrene, 

chrysene, benzo[a]anthracene, benzo[b]fluoranthene, benzo[k]fluoranthene, 

benzo[a]pyrene, dibenz[a,h]anthracene, benzo[g,h,i]perylene, and indeno[1,2,3,-

c,d]pyrene. 

Petrogenic PAH The sum of petrogenic PAH compounds (2-, 3-, and 4-ring PAH: naphthalenes [C0 - C4], 

acenaphthene, acenaphthylene, fluorene [C0 - C3], phenanthrenes [C0 - C4], 

dibenzothiophenes [C0 - C3], chrysenes [C1 - C4], and fluoranthenes/pyrenes [C1 - C3]). 

Pyrogenic/Petrogenic The ratio of pyrogenic PAH compounds to petrogenic PAH compounds is useful for 

determining the relative contribution of pyrogenic and petrogenic hydrocarbons and in 

differentiating hydrocarbon sources. 
18

3.0 RESULTS AND DISCUSSION 

The Results and Discussion for this report begin with the input of dissolved and 

particulate substances by rivers and then transition to the transport and distribution of 

dissolved and particulate substances in the coastal Beaufort Sea. Most of the data are for 

trace metals and organic carbon. The final two sections present some data for PAH and 

results of a spiking experiment. As a preview, the following seven sections make up the 

Results and Discussion. 

3.1 Source Rivers 2001: Transport of Dissolved and Particulate Metals and Organic 

Carbon. 

3.2 Source Rivers 2002: Transport of Dissolved and Particulate Metals and Organic 

Carbon. 

3.3 Transport of Dissolved and Particulate Metals and Organic Carbon by Rivers to 

the Coastal Beaufort Sea. 

3.4 Partitioning of Metals between Dissolved and Particulate Phases in Rivers. 

3.5 Dissolved and Particulate Metals in the Coastal Beaufort Sea. 

3.6 Dissolved and Particulate Organic Substances in Seawater. 

3.7 Spike Study for Polycyclic Aromatic Hydrocarbons 

3.1 Source Rivers 2001 

3.1.1 Transport of Water and Suspended Sediment 

Concentrations of dissolved and particulate metals (As, Ba, Ca, Cu, Fe, K, Mg, Mn, Na, 

Ni, Pb and Zn), particulate Al and dissolved and particulate organic carbon (DOC and 

POC) were determined for the Sagavanirktok, Kuparuk and Colville rivers (Figure 3-1 

and Table 3-1) during May to August 2001. Conductivity and concentrations of 

dissolved major elements (Ca, Mg, Na, K, bicarbonate and sulfate) were determined in 

river water to evaluate differences in composition and the degree of chemical weathering 

among rivers. 

 

Most rivers that drain into the Arctic Ocean carry 40 to 80% of their annual volume of 

water during peak flow in May, June and July (Arnborg et al., 1967; Gordeev et al, 

1996). Studies in the Alaskan Arctic have shown that concentrations of TSS in the 

Colville River follow the same trend as water flow with >70% of the annual discharge of 

TSS occurring during May and June (Arnborg et al., 1967). Large seasonal discharges of 

water and suspended sediment at high latitudes emphasize the importance of annual 

spring floods to the arctic hydrologic cycle. 

The three rivers studied during the ANIMIDA program, the Sagavanirktok, Kuparuk and 

Colville rivers (Figure 3-1), lie within the Arctic climatic zone where annual 

temperatures average -12°C and mean precipitation is ~12 cm/yr (Telang et al., 1991). 

The drainage basins of these Arctic rivers include the following three physiographic 

provinces: the Arctic Mountain Province, the Arctic Foothills Province, and the Arctic 

Coastal Plain Province (Payne et al., 1951). Based on the classification scheme proposed 
19

Figure 3-1. Map showing locations of sampling sites in the Colville, Kuparuk and 

Sagavanirktok rivers with inset map showing study area. 

Table 3-1. Locations of river sampling sites. 

Site Latitude (N) Longitude (W) 

Sagavanirktok River

(near Prudhoe Bay) 70° 15.033 ́ 148° 18.484 ́

Sagavanirktok River 

(~30 km upstream at mile 401 on 

the Dalton Highway) 70° 01.684 ́ 148° 37.781 ́

Sagavanirktok River 

(U.S.G.S. gauge at mile 327 on the 

Dalton Highway ) 

69° 00.527 ́ 148° 49.214 ́

Kuparuk River 70° 19.812 ́ 149° 00.527 ́

Colville River 70° 09.519 ́ 150° 56.791 ́

U.S.G.S. 

Mile 401 
20

by Craig and McCart (1975), the Sagavanirktok and Colville rivers can be classified as 

mountain streams that drain snowfields and glaciers in the Brooks Range. In contrast, the 

yellow-colored water of the Kuparuk River is more representative of a tundra stream 

(Lock et al., 1989). All three rivers flow into the coastal Beaufort Sea. 

Rivers are a major source of water and sediment to the ANIMIDA study area during 

spring runoff and on an annual basis. The river-borne water and sediment carry a full, 

natural complement of dissolved and particulate elements that are physically and 

chemically weathered from the mountains and tundra bordering the coastal Beaufort Sea. 

To understand possible anthropogenic perturbations to the ANIMIDA study area, one 

must first understand the composition, flow characteristics and amounts of incoming 

sediment and water. In this regard, the Sagavanirktok, Kuparuk and Colville rivers 

(Figure 3-1 and Table 3-1) were sampled during spring runoff (May-June) in 2001 and 

2002 and during the summers (July-August) of 2000, 2001, and 2002. During breakup, 

the Sagavanirktok River was sampled daily and the other two rivers were sampled every 

two to five days as logistics permitted. 

Water discharge data were taken from United States Geological Survey (U.S.G.S.) 

gauges on the Sagavanirktok (#15908000) and Kuparuk (#15896000) rivers (U.S.G.S., 

2001). The gauge on the Sagavanirktok River is located ~160 km upstream from the 

bridge near Prudhoe Bay where the daily samples were collected and the gauge 

incorporates only ~20% of the drainage basin. The U.S.G.S. gauge for the Kuparuk 

River is located <5 km upstream from our sampling location and receives water discharge 

from >90% of the drainage basin. Flow data for the Colville River were collected only 

during the period of peak flow by Baker et al. (2001); the U.S.G.S. does not maintain a 

gauge on the Colville River. 

Water began to flow in the Sagavanirktok River on June 3, 2001 (Figures 3-2 and 3-3). 

Samples were collected daily from June 3 to June 23 and later on July 30 and August 8 

from the bridge near the Prudhoe Bay Operations Center (PBOC). Samples also were 

collected at mile 401 on the Dalton Highway on June 5, 11, 12, 16, 19 and 21 and at the 

site of a gauging station (mile 327 on the Dalton Highway) maintained by the U.S.G.S. 

on June 14 and 21, about 150 km south of Deadhorse. 

 

Concentrations of TSS in the Sagavanirktok River at PBOC increased from ~40 mg/L on 

June 3, 2001, to 600 mg/L within 10 days on June 12 and then decreased to ~30 mg/L by 

June 18 (Figure 3-2). A secondary pulse occurred about June 23 when concentrations of 

TSS rose to ~90 mg/L following a rain storm (Figure 3-2). Data for water flow at the 

U.S.G.S. gauge, located ~150 km upstream, followed a similar trend. A 1- to 2-day 

offset between the peaks in TSS and water flow is due to the 150 km difference in 

location between the gauge and primary sampling site (Figure 3-1). Results for TSS in 

the Sagavanirktok River at mile 401 on the Dalton Highway and the U.S.G.S. gauge site 

(mile 327 on the Dalton Highway) were similar to results from the PBOC bridge, 

considering a lag time of several hours (mile 401) to 2 days (mile 327). 
21

6/1/01 6/8/01 6/15/01 6/22/01 

Water Discharge (m3/s)

0

100

200

300

400

Total Suspended Solids (mg/L)

0

100

200

300

400

500

600

700

TSS 

Water Flow Calculated

Water Flow Measured

Sagavanirktok River 2001

 6/1/2001 6/8/2001 6/15/2001 6/22/2001

Water Discharge (m3/s)

0

500

1000

1500

2000

Total Suspended Solids (mg/L)

0

25

50

75

100

TSS

Calculated Water Flow

Measured Water Flow

Kuparuk River 2001

June 2001

8 10 12 14

Water Discharge (m3/s)

2000

4000

6000

8000

10000

Channel Ice

 Intact

Channel Ice

 Clear

Colville River 2001

 

Colville River 2001

June 2001

0 2 4 6 8 10 12 14 16 18 20 22 24 26 28 30

TSS (mg/L)

0

100

200

300

400

500

600

Figure 3-2. Water flow and concentrations of total suspended solids (TSS) for the Sagavanirktok, 

Kuparuk and Colville rivers during June 2001. Water data for the Sagavanirktok and 

Kuparuk rivers are from the U.S. Geological Survey. Flow data for the Colville 

River during peak flow are from Baker et al. (2001); the U.S.G.S. does not maintain 

a water flow gauge on the Colville River. 
22

 Sagavanirktok River on May 25 and June 11, 2001 at bridge near Prudhoe Bay Operations 

Center. 

 Kuparuk River causeway/bridge (eastern segment of river) shown under water during peak flow 

on June 11, 2001 and then high and dry and rebuilt on June 20, 2001.

 

Colville River at Monument 1 during peak flow on June 9, 2001 and later at lower flow on June 

20, 2001. 

Figure 3-3. Sagavanirktok, Kuparuk and Colville rivers during June 2001. 

May 25, 2001 June 11, 2001 

June 11, 2001 June 20, 2001 

June 9, 2001 June 20, 2001 
23

The flow gauge in the Sagavanirktok River was not installed by the U.S.G.S. until the 

river was free of ice on June 10, 2001, ~7 days after water flow began. Thus, during 

2001 and most other years, the ascending limb of the hydrograph is calculated, not 

measured for the Sagavanirktok River. Furthermore, because the gauge is upstream in 

the western drainage basin of the Sagavanirktok River, the gauge covers only ~20% of 

the watershed and may not characterize flow patterns for the entire basin. During 2001, 

the total volume of water measured at the U.S.G.S. gauge in the Sagavanirktok River was 

~1.3 km3

, yielding a total extrapolated (from 20% to 100%) flow of ~6.5 km3 y

-1

(U.S.G.S., 2001). About 30% of the total annual water flow of Sagavanirktok River was 

discharged during June (Figure 3-2). 

The spring flood during June carried ~60% of the total annual water discharge in the 

Kuparuk River (Figures 3-2 and 3-3). In the Kuparuk River, concentrations of TSS 

reached peak values of 60 mg/L on June 10, 2001 and decreased to <5 mg/L after June 16 

(Figure 3-2). Peak flow recorded for the Kuparuk River was about 600 m3/sec on June 

12, 2001, decreasing to <50 m3

/sec after June 28, 2001. Values for TSS were ~0.6 mg/L 

during August 2001 for the Kuparuk River. 

Concentrations of TSS in the Colville River followed similar trends to those observed for 

the Sagavanirktok River with maximum levels of about 600 mg/L on June 13, 2001 

(Figures 3-2 and 3-3). Values for TSS were about 6 mg/L during August 2001 for the 

Colville River. During the spring snow melt, flow in the Colville River (6,000 to 9,000 

m3/sec) was an order-of-magnitude greater than in the Sagavanirktok or Kuparuk rivers. 

3.1.2 Trends in Concentrations of Dissolved Major Ions 

In the Sagavanirktok, Kuparuk and Colville rivers conductivity and concentrations of 

dissolved Ca and Mg and carbonate alkalinity (CA) decreased as discharge increased 

(Table 3-2, Figure 3-4). For example, concentrations of dissolved Ca decreased by 27% 

from 1450 μeq/L on June 3rd to 1060 μeq/L during maximum peak discharge on June 8th

in the Sagavanirktok River (Figure 3-4b). Carbonate alkalinity correlated well with 

concentrations of dissolved Ca + Mg (r = 0.98) for all three rivers and decreased by a 

grand average of ~21% during peak discharge (Figure 3-5). The strong correlation 

between Ca + Mg and CA with a slope close to 1 is typical of drainage basins containing 

primarily carbonate rocks. Concentrations of fluoride and sulfate also decreased during 

peak discharge in the Sagavanirktok River, but were below detection limits (F-

 <3 μeq/L 

and SO4

2- <4 μeq/L) in the Kuparuk River. Concentrations of sulfate were above 

detection limits in the Colville River, but were ~3 to 6 fold less than in the Sagavanirktok 

River during off-peak and peak discharge, respectively (Table 3-2). Elevated 

concentrations of sulfate and fluoride in the Sagavanirktok River were likely due to the 

lithology of the drainage basin as discussed below. Both the Sagavanirktok and Colville 

rivers extend into the Brooks Range whereas the Kuparuk River receives runoff only 

from the foothills and coastal plain, suggesting that potential sources of sulfate are 

located in the mountains. Concentrations of fluoride were slightly above detection limits 

(2-3 fold) in the Sagavanirktok River because phosphate rocks (possibly apatite) 

containing F are present in Lisburne Limestone, a geologic formation only exposed in the 
24 

Table 3-2. Conductivity (Cond.) and concentrations of total dissolved solids (TDS), calcium (Ca), magnesium (Mg), sodiu

(K), hydrogen ion (H+), carbonate alkalinity (CA), sulfate, chloride (Cl), fluoride (F), silicon (Si) and dissol

(DOC) in the Sagavanirktok, Kuparuk and Colville rivers during peak and off-peak discharge in June 2001. 

 *Meybeck, 1979 

ND = not detected. 

River Cond. (μS) TDS (μeq/L) Ca (μeq/L) Mg (μeq/L) Na (μeq/L) K (μeq/L) H+ (neq/L) CA (μeq/L) Sulfate (μeq/L) Cl (μeq/L) 

(μe

Peak Discharge 

Sagavanirktok 

(n = 10) 

Mean 

Std. Dev. 

Range

184 

± 24 

147-218

3410 

± 410 

2950-4150

1180 

± 120 

1060-1330

340 

± 80 

270-470

45 

± 10 

32-65

21 

± 8 

6-30

18 

± 4.4 

12-25

1430 

± 140 

1270-1700

355 

± 121 

225-569

44 

± 24 

19-83

± 

7

Kuparuk 

(n = 3) 

Mean 

Std. Dev. 

Range

67 

± 13 

56-81

1030 

± 140 

870-1140

380 

± 50 

330-440

90 

± 10 

80-90

36 

± 5 

30-39

30 

± 3 

27-32

47 

± 19 

33-69

462 

± 69 

383-504

ND 

63 

± 11 

50-71

N

Colville 

(n = 1) 

Mean 

Std. Dev. 

Range

55 1260 286 148 78 29 32 668 62 15 N

Off-Peak Discharge 

Sagavanirktok

(n = 10) 

Mean 

Std. Dev. 

Range

246 

± 11 

233-264 

4590 

± 260 

4250-4980

1480 

± 102 

1350-1630

540 

± 40 

500-590

53 

± 6 

46-68

10 

± 3 

8-15

9.7 

± 2.9 

7-15

1810 

± 91 

1660-1930

670 

± 55 

595-753

25 

± 5 

19-35

1

± 

11

Kuparuk 

(n = 3) 

Mean 

Std. Dev. 

Range

112 

± 3 

108-115

2010 

± 70 

1930-2060

744 

± 19 

722-760

140 

± 10 

130-150

46 

± 3 

44-49

16 

± 1 

15-17

19 

± 1.0 

17-19

1010 

± 48 

960-1040

ND 

64 

± 9 

53-69

N

Colville 

(n = 3) 

Mean 

Std. Dev. 

Range

111 

± 19 

90-125

1960 

± 300 

1610-2140

549 

± 57 

4490-593

270 

± 20 

250-290

110 

± 23 

83-126

34 

± 8 

24-39

27 

± 8.2 

20-36

783 

± 150 

615-880

212 

± 46 

159-243

27 

± 10 

16-35

N

World Average* - 1250 670 260 223 33 - 850 172 162 
25 

Figure 3-4. (a) Conductivity and concentrations of dissolved (b) calcium (Ca), (c) magnesium (Mg), (d) 

carbonate alkalinity, (e) sulfate and (f) fluoride (F) in the Sagavanirktok River (●) and 

Kuparuk River (▲) during June 2001. Concentrations of sulfate and F were below detection 

limits in the Kuparuk River. 

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Carbonate Alkalinity (μeq/L)

0

500

1000

1500

2000

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Dissolved Sulfate (μeq/L)

0

250

500

750

1000

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Dissolved Ca (μeq/L)

0

500

1000

1500

2000

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Dissolved Mg (μeq/L)

0

250

500

750

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Dissolved F (μeq/L)

0

5

10

15

20

5/28/01 6/4/01 6/11/01 6/18/01 6/25/01 

Conductivity (μS)

0

100

200

300

a. b.

c. d.

e. f.

Detection lImit Detection lImit
26 

Ca + Mg (meq/L)

0.0 0.5 1.0 1.5 2.0 2.5

Alkalinity ((meq/L)

0.0

0.5

1.0

1.5

2.0

2.5

Sagavanirktok

Kuparuk 

Colville

1:1

Figure 3-5. Concentrations of dissolved calcium plus magnesium (Ca + Mg) versus carbonate alkalinity 

in the Sagavanirktok, Kuparuk and Colville rivers. Line shows 1:1 relationship. 

drainage basin of the Sagavanirktok River (Payne et al., 1951). 

Concentrations of dissolved Si also decreased during peak discharge in the Sagavanirktok, 

Kuparuk and Colville rivers by 23%, 40% and 37%, respectively (Table 3-2). Low levels of 

dissolved Si in these rivers (18-46 μM) contrast sharply with the trend found in the Yukon River 

where concentrations of dissolved Si increase from ~120 μM to >180 μM during peak discharge 

(Edmond et al., 1996). This apparent discrepancy will be discussed below. 

In contrast to decreasing concentrations of Ca, Mg, CA, sulfate and F during peak discharge, 

concentrations of K, DOC and H+ (expressed as H+ activity in neq/L) increased during peak 

discharge (Figure 3-6). In the arctic, during peak discharge of snowmelt, runoff is confined to 

the upper-most organic soil horizon (O-horizon) and surface litter. As soils thaw, ions leached 

from organic matter or concentrated in soil interstitial water and pools of water on the tundra 

(ponds, lakes, boggy areas) are transported with snowmelt into rivers. This phenomenon results 

in increased concentrations of K and DOC and lower pH in river water during the spring floods. 
27 

Concentrations of dissolved K increased from 6 μeq/L on June 3 to ~30 μeq/L on June 8, 2001, 

and averaged 52% higher during peak than off-peak discharge in the Sagavanirktok River 

(Figure 3-6a, Table 3-2). Similar trends were found in the Kuparuk River. During off peak 

discharge, concentrations of dissolved K in both the Sagavanirktok and Kuparuk rivers were ~2 

to 3 fold lower than the world average (Table 3-2). In contrast, concentrations of dissolved K 

were similar to the world average in the Colville River during both peak and off- peak discharge. 

 

 

6/1/01 6/8/01 6/15/01 6/22/01 

Disolved K (μeq/L)

0

10

20

30

40

50

6/1/01 6/8/01 6/15/01 6/22/01 

H+ Activity (neq/ L)

0

20

40

60

06/01/01 06/08/01 06/15/01 06/22/01 

 Dissolved Organic Carbon (μM)

0

200

400

600

800

1000

06/01/01 06/08/01 06/15/01 06/22/01 

Dissolved Organic Carbon (μM)

0

300

600

900

1200

1500

a. b.

c. d.

7.2

7.4

7.7

pH

Figure 3-6. Concentrations of dissolved (a) potassium (K) and (b) hydrogen ion (H+) and pH in the 

Sagavanirktok (●) and Kuparuk (▲) rivers, and dissolved organic carbon in the (c) 

Sagavanirktok River and (d) Kuparuk River during June 2001. 
28 

Higher concentrations of dissolved K in the Colville River are consistent with known geology of 

the Colville Formation (Upper Cretaceous) where biotite, a K-rich mineral, was found to be 40-

70% of the heavy mineral assemblage (Payne et al., 1951). 

3.1.3 Interrelationships among Major Ions 

Factor analysis with varimax rotation (Reeder et al., 1972) was used to assess the relationships 

among dissolved Ca, Mg, Na, K, Cl, sulfate, F, CA, Si, H+, and DOC in the Sagavanirktok River 

for 2001. Significant positive loadings are shown in bold and negative loadings are italicized 

(Table 3-3). The results show that 3 factors explained ~90% of the variance among samples. 

 

Table 3-3. Varimax factor matrix of dissolved ions and dissolved 

organic carbon (DOC) for the Sagavanirktok River. 

Values listed in table are significant at p = 0.05. 

Element Factor (% of Variance Explained) 

 #1 (53%) #2 (24%) #3 (12%) 

Ca 0.89 

Mg 0.84 

K -0.64 0.66 

Na 0.99 

F 0.84 

Cl -0.69 0.53 

Sulfate 0.84 

CA 0.85 

H+ -0.50 0.55 

DOC 0.87 

Si 0.85 

Extraction Method: Principal Component Analysis. 

Rotation Method: Varimax with Kaiser Normalization. 

Factor 1 explains ~53% of the variance among analytes and is characterized by high positive 

scores for Ca, Mg, F, sulfate, CA, Si and moderately high negative scores for K, Cl, and H+ 

(Table 3-3). High positive scores for Ca, Mg, F, sulfate, and CA are consistent with chemical 

weathering of limestone, dolomite and S-bearing rock. Negative loadings for K, Cl, and H+

show that these chemical species are derived from different source minerals and are transported 

at high levels at peak flow as previously discussed. The elements with positive loadings for 

Factor 1 are transported at slightly lower concentrations during peak discharge. 

Factor 2 accounts for ~24% of the total variance with significant loadings for K, H+ and DOC. 

This factor supports an earlier discussion that increases in concentrations and sources of these 

three components are linked to the release of K, DOC and H+

 from vegetation, soils, ponds and 

surface water via the infiltration of snowmelt and subsequent discharge into the rivers. 
29 

Factor 3 has a strong positive loading for Na (0.99), a moderate positive loading for chloride 

(0.53) and explains ~12% of the variance among samples. The low concentrations of chloride 

are likely derived from inputs of cyclic salts, but additional sources of Na from feldspars are 

likely present. Therefore, the relationship between Na and Cl in Factor 3 is most likely derived 

between a cyclic salt source for both ions and an additional source for Na. 

3.1.4 Reconstruction of Chemical Weathering to Produce Major Ion Concentrations 

of Rivers 

Rember (2002) characterized the river-borne particles and reconstructed the composition and 

amounts of the minerals that were chemically weathered to yield the concentrations of the 

dissolved major ions found in the Sagavanirktok, Kuparuk and Colville rivers. The complete 

section from Rember (2002) is provided in Appendix D, including the details of the calculations. 

The dominant rock type that is chemically weathered in each of the three rivers is carbonate 

(limestone and dolostone) that accounts for >80% of the dissolved solids. 

During peak discharge in the Sagavanirktok River, a total of ~96 mg/L of rock was chemically 

weathered during peak discharge in the Sagavanirktok River, with ~34% from evaporites, 58% 

from carbonates and 8% from silicates (Figure 3-7). 

During off-peak discharge in the Sagavanirktok River, the amount of rock weathered increased 

to 136 mg/L (Figure 3-7, Sagavanirktok Off-Peak pie). This was consistent with the processes 

that occur during the spring floods in northern Alaska. During peak discharge, runoff is confined 

to the O-horizon and snowmelt is proceeding at a rapid rate. Therefore, the lack of an active 

layer, combined with a relatively short residence time (contact time) of the snowmelt in the 

drainage basin, does not allow minerals to undergo extensive chemical weathering. However, 

during off-peak discharge, the volume of snow melting decreases and therefore the residence 

time of snowmelt in the mountains and coastal plain probably increases allowing for increased 

chemical weathering of the rocks in the drainage basin. 

In the Kuparuk River drainage basin, ~28 and 46 mg/L of carbonate and silicate rock were 

weathered during peak and off-peak discharge respectively (Figure 3-8). These values are 

significantly lower (2-3 fold) than the amount of rock weathered in the Sagavanirktok River. 

This suggests that the chemical weathering of rocks from the Brooks Range (and additional 

sources of SO4

2-) have a large impact on the chemical composition of river water. In contrast to 

the Sagavanirktok and Colville rivers, no Na-silicate minerals were needed for the reconstruction 

of minerals weathered in the Kuparuk River, suggesting that the source of Na-silicates also may 

be primarily found in the Brooks Range. However, due to the lack of evaporites and relatively 

low concentrations of carbonates, silicate rock weathering accounted for ~20 and 9% of the total 

rock weathered in the drainage basin of the Kuparuk River during peak and off-peak discharge, 

respectively. 

The weathering of carbonates plus evaporites in the Colville River accounted for 76 and 81% of 

the rocks weathered during peak and off-peak discharge respectively (Figure 3-9). However, the 

amount of rock weathered was more similar to the Kuparuk than the Sagavanirktok River (Figure 
30 

3-9). As discussed above, evaporite and carbonate minerals are most abundant in the drainage 

basin of the Sagavanirktok River and are more rapidly weathered than silicate minerals. 

Sagavanirktok River Peak Discharge

Evaporite

Carbonate

Na-Silicate

K-Silicate

Total = 96 mg rock chemically weathered/L

Total = 136 mg rock chemically weathered/L

Sagavanirktok River Off-Peak Discharge

Evaporite

Carbonate

Na-Silicate

K-Silicate

34%

58%

6%

2%

46%

48%

2%

4%

Figure 3-7. Fraction of different rock types that were chemically weathered to produce the observed 

concentrations of dissolved major elements in the Sagavanirktok River during peak and offpeak flow in 2001. 
31 

Carbonate

K-Silicate

Total Rock Weathered = 28 mg/L

Total Rock Weathered = 46 mg/L

Kuparuk River Off-Peak Discharge

Carbonate

K-Silicate

Kuparuk River Peak Discharge

80%

20%

91%

9%

Figure 3-8. Fraction of different rock types that were chemically weathered to produce the observed 

concentrations of dissolved major elements in the Kuparuk River during peak and off-peak 

flow in 2001. 
32 

Colville River Peak Discharge

Evaporite

Carbonate

Na-Silicate (?)

K-Silicate

Total Rock Weathered = 36 mg/L

Total Rock Weathered = 60 mg/L

Colville River Off-Peak Discharge

Evaporite

Carbonate

Na-Silicate

K-Silicate

58%

18%

25%

53%

28%

13%

6%

Figure 3-9. Fraction of different rock types that were chemically weathered to produce the observed 

concentrations of dissolved major elements in the Colville River during peak and off-peak 

flow in 2001. 
33 

3.1.5 Dissolved Organic Carbon and Trace Metals 

During the first 5 days of discharge (June 3 to 7, 2001), concentrations of DOC in the 

Sagavanirktok River increased sharply from 2.0 to 8.9 mg/L, levels that are up to 6 times greater 

than during off-peak discharge (Figure 3-10, Table 3-4). Similar trends for concentrations of 

DOC also were observed in the Kuparuk and Colville rivers, where peak concentrations were 

15.8 and 13.2 mg/L, respectively (Table 3-4). Higher concentrations of soluble organic matter 

from soils, surface ponds and bottom sediment in the Kuparuk and Colville rivers, relative to the 

Sagavanirktok River, reflect differences in the nature of the drainage basins as described later in 

this report. 

During peak discharge in June 2001, average concentrations of DOC in the Sagavanirktok, 

Kuparuk and Colville rivers averaged 2 to 5 times higher than concentrations measured during 

off-peak discharge in June (Table 3-4). Increased concentrations of DOC during peak flow were 

amplified with respect to total transport by increases in water discharge. The spring thaw is 

clearly a key period for transport of DOC to the Arctic Ocean from the Alaskan Arctic. 

Concentrations of DOC also have been observed to increase during peak water discharge in 

many rivers of the world (Cauwet and Meybeck, 1987; Depetris and Paolini, 1991; Cauwet and 

Sidorov, 1996; Boyer et al., 1997). This phenomenon is caused when snowmelt or rising water 

levels percolate through litterfall and DOC-rich interstitial water in the upper soil horizon where 

concentrations of DOC can be >96 mg/L, (Boyer et al., 1997; Michaelson et al., 1998). Depetris 

and Paolini (1991) found that concentrations of DOC increased during a flooding event in the 

Parana River such that the discharge-weighted mean increased from ~6.0 mg/L up to 10.2 mg/L 

and more than doubled the transport rate of DOC. A positive correlation between DOC and 

6/1/01 6/8/01 6/15/01 6/22/01 6/29/01 

Water Discharge (m3 s-1)

0

100

200

300

400

Dissolved Organic Carbon (mg/L)

0

2

4

6

8

10

Water Discharge

DOC

Figure 3-10. Concentrations of dissolved organic carbon and water discharge for the Sagavanirktok River 

during June 2001 and 2002. Water flow data from U.S.G.S. (2001). 
34 

Table 3-4. Concentrations of total suspended solids (TSS), dissolved metals and dissolved organic carbon (DOC) in the 

and Colville rivers during peak and off-peak discharge in June 2001.

River Ba (μg/L) Cu (μg/L) Fe (μg/L) Pb (ng/L) Zn (μg/L) D

(m

Peak Discharge Sagavanirktok (n = 11) 

Mean Std. Dev. Range 

31.8 

± 2 

27.5-35.1 

0.79 

± 0.5 

0.57-0.96 

38.1 

± 24.0 

11.2-72.0 

27.8 

± 12.6 

15.5-46.6 

0.22 

± 0.11 

0.13-0.44 

5

± 

2.

Kuparuk (n = 5) 

Mean Std. Dev. Range 

19.5 

± 1.5 

18.0-21.0 

0.80 

± 0.08 

0.72-0.86 

212 

± 27 

181-232 

53.0 

± 0.8 

52.4-53.9 

0.38 

± 0.3 

0.36-0.41 

1

± 

12.

Colville (n = 3) 

Mean Std. Dev. Range 

50.7 

± 3.6 

46.7-53.8 

2.5 

± 0.2 

2.2-2.7 

80.9 

± 29.9 

59.9-102 

60.1 

± 9.3 

53.5-66.5 

0.14 

± 0.02 

0.11-0.17 

1

± 

8.0

Off-Peak Discharge Sagavanirktok (n = 9) 

Mean Std. Dev. Range 

31.6 

± 0.3 

30.9-31.7 

0.40 

± 0.1 

0.29-56 

6.8 

± 2.9 

2.8-9.5 

13.5 

± 5.8 

7.0-19.1 

0.12 

± 0.04 

0.08-0.16 

2

± 

1.4

Kuparuk (n = 5) 

Mean Std. Dev. Range 

23.5 

± 2.2 

18.5-26.6 

0.77 

± 0.04 

0.71-0.81 

64.2 

± 21.3 

36.7-116 

40.6 

± 13.3 

21.8-59.7 

0.29 

± 0.01 

0.27-0.31 

8

± 

8.

Colville (n = 3) 

Mean Std. Dev. Range 

51.6 

± 3.3 

49.3-53.4 

1.6 

± 0.1 

1.5-1.7 

50.3 

± 43.0 

19.9-80.4 

40.6 

± 8.9 

27.6-50.6 

0.26 

± 0.1 

0.19-0.33 

5

± 

4.
35

water flow also was reported for the Lena River where concentrations of DOC were at least 30 to 

40% higher during the spring floods than during September (Cauwet and Sidorov, 1996). 

Concentrations of dissolved Fe, Cu, Pb and Zn followed trends shown for DOC (Figure 3-11). 

In the Sagavanirktok River, concentrations of dissolved Fe increased sharply from 3 to 72 μg/L 

in ~7 days. Then, as flow decreased, concentrations of dissolved Fe returned to ~3 mg/L within 

8 days of maximum levels. Concentrations of dissolved Cu, Pb and Zn in the Sagavanirktok 

River also increased to maximum levels during peak flow (Figure 3-11). These values at peak 

discharge are approximately 3, 5.5 and 6 times greater, respectively, than during off-peak 

discharge and occurred at a time when water flow was ~250% greater at the Sagavanirktok River 

gauge, indicating that net transport of dissolved metals, like DOC, was greatly enhanced during 

peak discharge. 

06/01/01 06/08/01 06/15/01 06/22/01 

Dissolved Fe (

μg/L)

0

20

40

60

80

100

06/01/01 06/08/01 06/15/01 06/22/01 

 Dissolved Zn (

μg/L)

0.0

0.1

0.2

0.3

0.4

0.5

0.6

06/01/01 06/08/01 06/15/01 06/22/01 

 Dissolved Pb (ng/L)

0

10

20

30

40

50

60

06/01/01 06/08/01 06/15/01 06/22/01 

Dissolved Cu (

μg/L)

0.0

0.2

0.4

0.6

0.8

1.0

1.2

Figure 3-11. Concentrations of dissolved iron (Fe), copper (Cu), lead (Pb) and zinc (Zn) in the 

Sagavanirktok River during June 2001. 
36

Strong correlations (r ≥ 0.82) were found for DOC versus Cu, Fe, Pb and Zn (Table 3-5). The 

trends, correlations and timing for peak levels of trace metals and DOC support the idea that 

metals and DOC are strongly influenced by the discharge of soil interstitial water and shallow 

surface water that is diluted by melt water and flushed from surrounding soils into the 

Sagavanirktok River. During the short summers, the arctic coastal plain is covered with pools of 

standing water and lakes where DOC accumulates and trace metals are leached from soils. The 

permafrost, along with a topography that averages <2 m on the coastal plain, inhibit lateral water 

flow during the summer months, thereby extending the residence time of the surface water in the 

system. Then, increased surface runoff in the spring, after the long frozen winter (8 to 9 months), 

provides a direct pathway for the release of accumulated DOC and dissolved metals into the 

rivers from the thawing ponds and soils. 

Table 3-5. Pearson’s correlations between dissolved trace metals and dissolved 

organic carbon (DOC) in the Sagavanirktok River during June 

2001. All correlations are significant at p = 0.01. 

Average concentrations of dissolved Fe, Pb, Zn and organic carbon in the Kuparuk River during 

peak and off-peak discharge were ~2 to 5 times higher than in the Sagavanirktok River (Table 3-

4). Concentrations of dissolved Cu in the Kuparuk River were not significantly different (t-test, 

α=0.5) during peak versus off-peak flow. Data collected from the Colville River showed similar 

trends to those for the Sagavanirktok and Kuparuk rivers. During peak discharge, average 

concentrations of DOC, Cu, Fe and Pb in the Colville River were 1.5 to 2 times higher than 

during off-peak flow (Table 3-4). In general, concentrations of dissolved metals and DOC in the 

Colville River were higher than those found in the Sagavanirktok River, but less than in the 

Kuparuk River (Table 3-4). 

The higher concentrations of DOC and dissolved metals in both the Kuparuk and Colville rivers, 

relative to the Sagavanirktok River, are most likely related to differences in lithology and soil pH 

(organic acids). Previous studies have shown that the Sagavanirktok River drains primarily 

limestone deposits and has concentrations of dissolved Ca that are ~2 times higher than in the 

Kuparuk and Colville rivers (Telang et al., 1991). Walker and Webber (1979) show that 

westward of the carbonate-rich Sagavanirktok River, soil pH decreases from >7 to <6 as the 

tundra shifts from wet alkaline to wet acidic because soils become rich in organic acids. Other 

studies have shown that soil pH can decrease to 4.2 in tussock tundra and heath ecosystems 

(Valentine and Binkley, 1992). In addition, Parkinson (1977) found an inverse relationship 

between calcium carbonate equivalents and organic matter concentration in the region. These 

data suggest that soils within the Kuparuk and Colville drainage basins may undergo more 

intense chemical weathering due to higher concentrations of organic acids and lower pH. 

Cu Fe Pb Zn 

Cu 1 

Fe 0.86 1 

Pb 0.89 0.93 1 

Zn 0.79 0.90 0.90 1 

DOC 0.82 0.90 0.91 0.87 
37

Concentrations of dissolved Cu, Fe, Pb, Zn and DOC from this study in the Alaskan Arctic 

during July and August 2001, when water flow was greatly reduced (<50 m3/sec), are consistent 

with concentrations found in other arctic rivers during the months of August and September 

(Table 3-6). For example, concentrations of dissolved Pb during August in the Sagavanirktok, 

Kuparuk and Colville rivers are within the range of concentrations found in the Lena, the Ob and 

the Yenisey rivers during September and are 2 to 6 times lower than the world average (Table 3-

6). Concentrations of dissolved Pb in the Sagavanirktok and Kuparuk rivers are lower than 

concentrations found in a mountain watershed in Sierra Nevada, California where Pb 

concentrations were ~8.7 ng/L (43 pM) and considered to be natural levels for river water (Erel 

et al., 1991). Lower concentrations of dissolved metals in arctic rivers during the summer and 

fall suggest that anthropogenic contamination is minimal and that spring discharge in the 

Alaskan Arctic provides an important transport mechanism for DOC and organically-bound, 

dissolved metals. 

Table 3-6. Ranges and average concentrations of dissolved metals and dissolved organic carbon (DOC) 

during August and September (off peak) in rivers of the Alaskan and Russian Arctic. 

 

(1) Guieu et al., 1996; (2) Guay and Falkner, 1998 (3) Cauwet and Sidorov, 1996; (4) Martin et al., 

1993; (5) Dai and Martin, 1995; (6) Martin and Windom, 1991; (7) Meybeck, 1982 

In contrast with Cu, Fe, Pb and Zn, concentrations of dissolved Ba in the Sagavanirktok River 

varied by only ± 7% (coefficient of variation, CV = [standard deviation/mean) x 100] during 

peak discharge (Table 3-4, Figure 3-12). Concentrations of dissolved Ba were even less variable 

(CV < 1%) during off-peak discharge (Table 3-4, Figure 3-12). Dissolved Ba concentrations 

decreased by up to 25% when water flow increased by 250% at the Sagavanirktok gauge. These 

data indicate that concentrations of dissolved Ba were not enhanced by the flushing of metals 

from soils and were only slightly affected by dilution during peak flow. 

River Reference Ba 

(μg/L )

Cu 

(μg/L ) 

Fe 

(μg/L ) 

Pb 

(ng/L) 

Zn 

(μg/L ) 

DOC 

(mg/L)

Sagavanirktok (this study) 39 0.29 2.1 7.0 0.03 1.1 

Kuparuk (this study) 33 0.95 10.3 4.4 0.03 6.3 

Colville (this study) 74 0.70 3.8 11.6 0.03 3.8 

Lena 1, 2, 3 18 0.76-0.95 24-47 - 0.08 5.9-7.9 

Lena 4 - 0.62 22.9 17 0.04 - 

Ob-Irtysh 3, 5 14 1.8-2.4 24-37 11-17 - 7.4-9.9 

Yenisey 3, 5 17 1.4-1.9 14-18 5-6 - 4.0 

World Average 6, 7 - 1.5 40 31 0.6 5.8 
38

06/01/01 06/08/01 06/15/01 06/22/01 

Dissolved Ba (μg/L)

0

10

20

30

40

50

60

Figure 3-12. Concentrations of dissolved barium (Ba) in the Sagavanirktok River during June 2001. The 

solid line is the mean value and dashed lines represent ±2 standard deviations from the 

mean. 

Concentrations of dissolved Ba in the Sagavanirktok, Kuparuk, and Colville rivers are within the 

range of 19 to 79 μg/L reported by Guay and Falkner (1998) for arctic rivers of North America. 

These data support the conclusion by Guay and Falkner (1998) that concentrations of dissolved 

Ba in Arctic rivers of North America are higher than those determined for any of the Eurasian 

Arctic rivers (Table 3-6). Guay and Falkner (1998) suggested that differences in concentrations 

between arctic rivers in North America and Eurasia are due to the chemical composition and 

weathering characteristics within their respective drainage basins. As discussed below, data 

from this study suggest that partitioning of Ba between the dissolved and particulate phases may 

control concentrations of dissolved Ba in rivers of the Alaskan Arctic. 

3.1.6 Particulate Trace Metals and Organic Carbon 

Concentrations of particulate Cu, Pb, Zn (μg/g dry weight), Fe and OC (% dry weight) in the 

Sagavanirktok River were more uniform than observed for the dissolved species (Figure 3-13). 

In general, concentrations of Cu (CV = 8.5%), Pb (CV = 11%), and Zn (CV =5.7%) were less 

variable than concentrations of Fe (CV =16%) and POC (CV =31%) (Table 3-7). In sharp 

contrast with dissolved Cu, Fe, Pb and Zn, particulate concentrations of these four metals were 

poorly correlated with organic carbon (r < 0.15), and relatively well correlated with particulate 

Al (Table 3-8). The poor correlations for POC versus Cu, Fe, Pb and Zn suggest that POC does 

not play a significant role in controlling concentrations of particulate trace metals in the 

Sagavanirktok River, but that the aluminosilicate (clay) content is more important. 
39

06/01/01 06/08/01 06/15/01 06/22/01 

Ba (μg g-1)

0

500

1000

1500

06/01/01 06/08/01 06/15/01 06/22/01 

Cu (μg g-1)

0

20

40

60

06/01/01 06/08/01 06/15/01 06/22/01 

Fe (%)

0

2

4

6

06/01/01 06/08/01 06/15/01 06/22/01 

Pb (μg g-1)

0

10

20

30

40

06/01/01 06/08/01 06/15/01 06/22/01 

Zn (μg g-1)

0

50

100

150

200

250

06/01/01 06/08/01 06/15/01 06/22/01 Particulate Organic Carbon (%)

0

1

2

3

4

5

Figure 3-13. Concentrations of particulate barium (Ba), copper (Cu), iron (Fe), lead (Pb), zinc (Zn) and 

particulate organic carbon (POC) in the Sagavanirktok River during June 2001. The solid 

line shows mean concentrations in each plot and dashed lines represent ±2 standard 

deviations from the mean. 
40

Table 3-7. Concentrations of particulate trace metals and particulate organic carbon (POC) in the 

Sagavanirktok, Kuparuk and Colville Rivers during June 2001. Peak and off-peak 

concentrations are presented for the Kuparuk River due to distinct differences in the 

concentrations of some trace metals during those periods. 

Table 3-8. Correlations for particulate trace metals and particulate organic carbon 

(POC) in the Sagavanirktok River during June 2001. 

** Correlation is significant at the 0.01 level. 

 * Correlation is significant at the 0.05 level. 

River Al 

(%) 

Ba 

(μg/g) 

Cu 

(μg/g) 

Fe 

(%) 

Pb 

(μg/g) 

Zn 

(μg/g) 

POC 

(%) 

Sagavanirktok 

Mean 

Std. Dev. 

Range

5.6 

± 0.9 

4.0-7.7

702 

± 113 

542-1008

32.8 

± 2.8 

29.7-39.2

3.3 

± 0.4 

2.6-4.0

18.0 

± 2.0 

16.0-23.4

123 

± 7 

115-135

1.60 

± 0.49 

0.7-2.7

Kuparuk 

Peak Discharge 

Mean 

Std. Dev. 

Range 

5.2 

± 0.5 

4.6-5.8 

615 

± 88 

497-743 

32.3 

± 5.8 

25.7-37.2 

3.6 

± 0.2 

3.3-3.8 

15.7 

± 0.7 

14.7-16.6 

124 

± 13 

110-145 

4.6 

± 1.1 

3.3-5.9 

Kuparuk 

Off-Peak Discharge 

Mean 

Std. Dev. 

Range 

3.5 

± 0.5 

2.7-4.0 

469 

± 70 

397-559 

29.9 

± 1.3 

28.6-31.2 

3.7 

± 0.3 

3.1-4.2 

14.4 

± 8.3 

4.0-22.5 

92.1 

± 21 

69-116 

4.9 

± 2.0 

2.8-7.6 

Colville 

Mean 

Std. Dev. 

Range

8.3 

± 0.3 

8.0-8.9 

989 

± 125 

890-1190

40.8 

± 2.3 

36.9-42.6

5.0 

± 0.3 

4.7-5.3

24.0 

± 6.8 

19.8-36.0

130 

± 11 

116-147

2.24 

± 0.56 

1.7-3.3

Al Ba Cu Fe Pb Zn 

Al 1 

Ba 0.91** 1 

Cu 0.78** 0.80** 1 

Fe 0.97** 0.89** 0.78** 1 

Pb 0.79** 0.88** 0.87** 0.76** 1 

Zn 0.76** 0.66** 0.53* 0.64** 0.62 1 

POC -0.14 0.11 0.14 -0.07 0.01 -0.13 
41

The trends in concentrations of particulate Ba in the Sagavanirktok River follow closely with 

those observed for Fe, suggesting that concentrations of particulate Ba also are controlled by the 

aluminosilicate content of the suspended solids (Figure 3-14). The correlation coefficient for 

particulate Al and Ba (r = 0.91) for the Sagavanirktok River indicates that variations in 

particulate Ba concentrations result from shifts in Al concentrations during peak and off-peak 

discharge (Figure 3-14). To further illustrate this relationship, concentrations of particulate Ba 

from the Kuparuk and Colville rivers were pooled with data for the Sagavanirktok River. The 

data in Figure 3-14a include values from all three rivers with a range of ~2 to >600 mg/L for 

TSS, and concentrations of POC ranging from <1 to >7%. Therefore, variations in 

concentrations of particulate Ba in the Sagavanirktok, Kuparuk and Colville rivers result mainly 

from dilution of fine-grained aluminosilicates by larger-grained sands and other nonaluminosilicate minerals. 

Al (%)

0 2 4 6 810

Fe (%)

0

2

4

6

8

Sagavanirktok 2001

Kuparuk 2001

Colville 2001

Sagavanirktok 2002

Kuparuk 2002 

Trend lines from

sediment data

Low Flow

(b)

Figure 3-14. Concentrations of particulate aluminum (Al) versus (a) barium (Ba) and (b) iron (Fe) for the 

Sagavanirktok, Kuparuk, and Colville rivers during June 2001 and 2002. Solid lines are 

from a linear regression for sediment data from the ANIMIDA study area and dashed lines 

show 99% prediction interval for sediment data. Data points for off-peak discharge in the 

Kuparuk River were not included in the linear regression for the Al vs. Fe plot. 

During peak discharge, as the banks of the Kuparuk River eroded and the river transported 

higher concentrations of TSS (> 50 mg/L), concentrations of particulate Fe, Pb and Zn correlated 

well (r = 0.98, 0.76, 0.93, respectively) with levels of particulate Al and the metal/Al ratios 

agreed within 15% with the results found for the Sagavanirktok River (Figure 3-14). However, 

when TSS concentrations decreased to an average of 4 mg/L in the Kuparuk River during low 

flow, the average Fe/Al ratio increased by ~35% relative to the Sagavanirktok River (Figure 3-

14). These data suggest that elevated concentrations of particulate Fe (6400 nM or 3.7% dry 

weight) relative to Al (14600 nM or 3.5% dry weight) during low flow (Figure 3-14) may be 

influenced by high concentrations of dissolved Fe (>60 μg/L) in the Kuparuk River that 

potentially enhance the formation of Fe hydrous oxides and increase concentrations of particulate 

Fe. Similarly, concentrations of particulate Pb and Zn increased with Fe and were elevated 

Al (%)

0 2 4 6 8 10

Ba (

μg/g)

0

500

1000

1500 Sagavanirktok 2001

Kuparuk 2001

Colville 2001

Sagavanirktok 2002 

Kuparuk 2002 

Trend lines from 

sediment data

(a)
42

above levels that would be predicted from the Al concentration and possibly result from 

scavenging by hydrous Fe-oxides. 

Concentrations of particulate Cu, Fe and Pb in the Colville River averaged 25 to 40% higher than 

concentrations found in the Sagavanirktok and Kuparuk rivers (Table 3-7). However, particles 

from the Colville River also had 50% higher concentrations of Al indicating that sources of 

suspended sediment in the western Brooks Range are richer in fine-grained aluminosilicates or 

less diluted by non-aluminosilicate minerals (Table 3-7). 

3.1.7 Major Elements in Suspended Solids 

Concentrations of particulate Al, Fe, Ca, Mg, K and Na were determined for the Sagavanirktok, 

Kuparuk and Colville rivers (Table 3-9). Concentrations of particulate Ca in the Sagavanirktok, 

Kuparuk and Colville rivers did not correlate well with Al (r < 0.2) (Figure 3-15). In the 

Kuparuk and Colville rivers, average concentrations of particulate Ca were ~6 to 10 fold lower 

than concentrations found in the Sagavanirktok River. The poor correlation for Ca with Al 

(r<0.2) suggests that the fraction of particulate Ca derived from aluminosilicate minerals was 

small. In addition, these data agree with dissolved Ca and CA data from this study and suggest 

that rocks in the drainage basin of the Sagavanirktok River are more carbonate-rich than those in 

the drainage basins of the Kuparuk and Colville rivers. 

Table 3-9. Concentrations of particulate metals (as % dry weight) in the Sagavanirktok, 

Kuparuk and Colville Rivers during June 2001. 

 

River Al 

(%) 

Ca 

(%) 

Fe 

(%) 

K 

(%) 

Mg 

(%) 

Na 

(%) 

Sagavanirktok 

(n = 22) 

Mean 

Std. Dev. 

Range

5.6 

± 0.9 

4.0-7.7

6.7 

± 0.99 

4.9-8.9

3.3 

± 0.4 

2.6-4.0

1.7 

± 0.25 

1.4-2.3

0.85 

± 0.11 

0.7-1.2

0.30 

± 0.03 

0.24-0.37

Kuparuk 

(n = 8)

Mean 

Std. Dev. 

Range 

4.4 

± 1.04 

2.7-5.8 

1.0 

± 0.2 

0.8-1.5 

3.7 

± 0.4 

3.1-4.2 

1.1 

± 0.2 

0.6-1.3 

0.46 

± 0.20 

0.12-0.69 

0.39 

± 0.07 

0.32-0.50 

Colville 

(n = 6) 

Mean 

Std. Dev. 

Range

8.3 

± 0.3 

8.0-8.9 

0.70 

± 0.30 

0.60-1.2 

5.0 

± 0.3 

4.7-5.3

2.0 

± 0.07 

1.9-2.1

1.1 

± 0.20 

0.8-1.2

0.51 

± 0.08 

0.39-0.59
43

Al (%)

0 2 4 6 8 10

Ca (%)

0

3

6

9

12

15

Sagavanirktok R.

Kuparuk R. 

Colville R.

Al (%)

0 2 4 6 8 10

K (%)

0

1

2

3

4

Al (%)

0 2 4 6 8 10

Na (%)

0.0

0.2

0.4

0.6

0.8

1.0

Al (%)

0 2 4 6 8 10

Mg (%)

0.0

0.5

1.0

1.5

2.0

Figure 3-15. Concentrations of particulate aluminum (Al) versus (a) calcium (Ca), (b) magnesium 

(Mg), (c) sodium (Na) and (d) potassium (K) for the Sagavanirktok, Kuparuk and 

Colville rivers during June 2001. 

Correlations for Mg versus Al in the Sagavanirktok River (r = 0.89) and combined Kuparuk and 

Colville rivers (r = 0.95) were high (Figure 3-15). However, the ratio of Mg to Al in the 

Sagavanirktok River (0.15 ± 0.02) was statistically greater (t-test, α = 0.05) than the ratio for the 

Kuparuk (0.10 ± 0.03) and Colville (0.13 ± 0.02) rivers. These data indicate that the suspended 

solids in the Sagavanirktok River were slightly enriched with Mg relative to the Kuparuk and 

Colville rivers. In addition to the good correlation for Mg versus Al, concentrations of Mg also 

correlated well with Fe in the Sagavanirktok River and Colville rivers (r = 0.80) (Figure 3-15). 

Therefore, Mg- and Fe-bearing aluminosilicate minerals (e.g., chlorite, biotite) present in the 

drainage basin of the Sagavanirktok, Kuparuk and Colville rivers are more likely to be potential 

sources of particulate Mg as discussed below (Payne et al., 1951; Darby et al., 1989). 

The good correlation for dissolved Ca versus Mg in the Sagavanirktok, Kuparuk and Colville 

rivers supports carbonate weathering as the dominant source of dissolved Ca and Mg. However, 
44

the poor correlation of Ca versus Mg in the suspended solids from each river suggests that 

carbonates are not highly abundant in the particulate fraction. The correlations found for Mg 

versus Fe and Al suggest that the aluminosilicate fraction is not highly weathered and does not 

greatly contribute to concentrations of dissolved Mg in the Sagavanirktok, Kuparuk and Colville 

rivers. 

Concentrations of particulate K averaged 1.7%, 1.1% and 2.0% in the Sagavanirktok, Kuparuk 

and Colville rivers (Table 3-9). In addition, concentrations of particulate K correlated well with 

the concentration of Al in the suspended solids (Figure 3-15). Similar to the results found for 

Mg, particles in the Sagavanirktok River were slightly enriched in K (K:Al = 0.31 ± 0.03) 

relative to the Kuparuk (0.24 ± 0.03) and Colville rivers (0.24 ± 0.03). 

Average concentrations of particulate Na were determined to be ~25 and 40% higher, in the 

Kuparuk and Colville rivers, respectively, than in the Sagavanirktok River (Table 3-9). 

However, no distinct trends or relationships were found for Na versus Al (Figure 3-15). 

The concentrations of Al, Fe, K, Mg and Na in suspended sediment from the Sagavanirktok and 

Kuparuk rivers were less than average values for continental crust (Wedepohl, 1995). However, 

concentrations of particulate Ca in the Sagavanirktok River averaged 1.7 fold greater than 

average values for continental crust and agreed with previous observations that carbonates 

dominate the lithology of the Sagavanirktok River drainage basin. Concentrations of particulate 

Al, Fe and K were similar to average values for continental crust in the Colville River. Higher 

concentrations of K-silicates are consistent with observations that the Colville River drains a 

relatively larger proportion of exposed K-rich silicate minerals (biotite) from the Cretaceous 

(Payne et al, 1951). In all cases, concentrations of particulate Mg and Na were less than average 

values for continental crust. 

3.2 Source Rivers 2002 

3.2.1 Overview and Transport of Water and Suspended Sediment 

Spring breakup in the Sagavanirktok River for 2002 was very different from what was observed 

in 2001. First, the start of river flow was almost two weeks earlier (May 20, 2002 versus June 2, 

2001). Second, after flow had been ongoing for about one week, the air temperatures cooled 

well below freezing and the river refroze (Figures 3-16 and 3-17). The same trend was observed 

offshore as river water initially flowed out over and under the ice and then the surface layer of 

river water froze over the 2-m thick layer of winter ice. The river re-thawed within four days, 

but water flow was less than during the earlier discharge period (Figure 3-17). 

The TSS and turbidity data for 2002 showed the same initial steep increase in levels of 

suspended particles to ~350 mg/L (Figure 3-17), similar to, but lower than the observed peak 

TSS of ~600 mg/L in 2001 (Figure 3-2, page 21). However, subsequent cold temperatures and 

freezing of the river truncated the flooding process and led to TSS levels <10 mg/L on May 31, 

2002, the final day of sampling before the ice prevented sampling for two days. Then, as the 

river re-melted, the increase in flow led to another peak in discharge of suspended sediment at 

>200 mg/L (Figure 3-17). Data for turbidity are shown on Figure 3-17 to point out that turbidity 
45

Sagavanirktok River at bridge near Prudhoe Bay Operations Center flowing on May 22, 2002, 

and re-frozen on May 29, 2002.

Kuparuk River during and after three-day flood period in May 2002. 

 

 

Colville River during June 2002. 

 

Figure 3-16. Sagavanirktok, Kuparuk and Colville rivers during May-June 2002. 

May 22, 2002 May 29, 2002 

May 23, 2002 May 25, 2002 

June 12, 2002 June 3, 2002 
46

05/20/02 05/27/02 06/03/02 06/10/02 06/17/02 

TSS (mg/L) and Turbidity (NTU)

0

50

100

150

200

250

300

350

400

Turbidity (NTU) 

TSS (mg/L)

Sagavanirktok River 2002

river froze

river re-melted

river flood begins

rain 

Figure 3-17. (a) Concentrations of total suspended solids (TSS) and turbidity for the Sagavanirktok River 

during May-June 2002 and (b) Water discharge (from U.S. Geological Survey) in 

Sagavanirktok River for June 2002. 

data are available for all water samples (Appendix A) and that the two indicators of suspended 

sediment levels track one another very well. Unfortunately, the U.S.G.S. was not able to install 

their gauge for water flow until June 6, 2002 (Figure 3-17), and therefore no data are available 

for the events described above. 

Conductivity in the Sagavanirktok River followed a more compressed trend in 2002 with a 

shorter time of 4 days at <200 μS (Figure 3-18) relative to the 8-day period of water flow with 

conductivity <200 μS observed in 2001 (Figure 3-4, page 25). Concentrations of TSS decreased 

to ~3 mg/L in late June and were ~1 mg/L in August, similar to levels observed in 2001. 

 

05/27/02 06/03/02 06/10/02 06/17/02 06/24/02 

Water Discharge (m3/s)

0

100

200

300

400

500

USGS Gauge Installed 6/6/2002

Sagavanirktok River 2002

(a) 

(b) 
47

05/20/02 05/27/02 06/03/02 06/10/02 06/17/02 

Conductivity (μS)

0

50

100

150

200

250

300

Sagavanirktok

Kuparuk 

Colville Conductivity

Figure 3-18. Conductivity in the Sagavanirktok, Kuparuk and Colville rivers during May-June 

2002. 

During 2002, we were fortunate to directly observe and sample the Kuparuk River during its 

brief (1 to 2 day) flood (Figures 3-16 and 3-19). The strong pulse of water that characterizes 

flooding in the Kuparuk River occurred on May 23, 2002. The flood receded by May 25 (Figure 

3-16). The complete flood cycle in the Kuparuk River occurred before the onset of colder 

temperatures and refreezing of the rivers. 

 

. 

05/27/02 06/03/02 06/10/02 06/17/02 06/24/02 

Water Discharge (m3/s)

0

100

200

300

400

500

600

USGS Gauge Installed 5/27/2002

Kuparuk River 2002

 

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

TSS (mg/L)

0

40

80

120

160

Kuparuk River 2002

 

Figure 3-19. Water flow and concentrations of total suspended solids (TSS) and turbidity for the Kuparuk 

River during May-June 2002 (flow data from U.S. Geological Survey). 

Maximum levels of TSS in the Kuparuk River during 2002 (Figure 3-19) were double maximum 

levels of ~60 mg/L during 2001. The higher levels of TSS observed during 2002 are most likely 

due to sampling at peak flow. Turbidity and concentrations of TSS in the Kuparuk River during 

both years may have peaked at higher levels than we observed (Figure 3-19). Unfortunately, due 

to washing out of the road and the intense flow conditions, we were able to sample only the 

eastern-most braid of the river during peak flow in both 2001 and 2002. Conductivity in the 

Kuparuk River during 2002 (Figure 3-18) followed a similar trend at similar values to those 

observed in 2001 (Figure 3-4, page 25) with a minimum of ~50 μS at peak flow, increasing to 

~120 μS after the spring flood receded. 
48

Access to the Colville River by helicopter was limited during 2002 due to the early onset of the 

spring floods and an increased focus on the under-ice effort near Prudhoe Bay. Data from Baker 

et al. (2002) show a short, strong pulse of water at >6000 m3/sec for 4-5 days (Figure 3-20). 

Duplicate samples for TSS on May 27, 2002, showed levels >600 mg/L. Levels of TSS 

decreased to 112 mg/L on June 3 and to <50 mg/L on and after June 12. Conductivity for the 

Colville River during the 2002 flood (Figure 3-18) event was similar to that observed in 2001 

(Table 3-12). During both years, the Colville River had the lowest conductivity of the three 

rivers, most likely due to the high water flow of the river and greater dilution of dissolved solids. 

May 2002

24 26 28 30

Water Discharge (m3/s) 2000

4000

6000

8000

10000

Channel Ice

 Clear

 

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02

TSS (mg/l)

0

100

200

300

400

500

600

700

Figure 3-20. Water flow and concentrations of total suspended solids (TSS) in the Colville River 

during May-June 2002. Flow data from Baker et al. (2002). 

3.2.2 Trends in Concentrations of Dissolved Major Ions 

Concentrations of major dissolved ions Ca, Mg, Na, K, Cl, sulfate, F and alkalinity (HCO3

-

 + 

CO3

2-) also were determined for river water samples collected during May-June 2002 (Table 3-

10). Concentrations of dissolved Ca, Mg and sulfate (Figure 3-21) followed similar patterns in 

the Sagavanirktok River during May-June 2002 and June 2001. Concentrations of each ion 

decreased during peak flow. The more complex flow pattern for the Sagavanirktok River during 

2002 did not alter concentrations during peak flow. Concentrations of dissolved Ca, Mg and 

sulfate (Figure 3-21) in the Kuparuk River for 2002 were similar to those observed in 2001; and 

the trend in concentrations also showed decreased levels during peak flow. 

In contrast to decreasing concentrations of Ca, Mg, CA, sulfate and F during peak discharge 

(Table 3-10 and Figure 3-21), concentrations of K increased during peak discharge in both the 

Sagavanirktok and Kuparuk rivers (Figure 3-22). The trend is similar to that described for the 

spring floods of 2001. Peak concentrations of DOC were observed during the spring floods of 

2002 in the Kuparuk River, but not in the Sagavanirktok River (Figure 3-23). This distinction 

was most likely due to the thawing and refreezing processes and how they retarded to release of 

DOC from the soil active layer. The Kuparuk River went through a complete discharge process 

prior to the period of refreezing that occurred; however, the spring flood in the Sagavanirktok 

River did reach completion prior to the period of refreezing. Because of the strong similarities in 

concentrations of major ion between 2002 and 2001, the same statistical and chemical 

weathering calculations were not repeated. 
49

Table 3-10. Conductivity (Cond.) and concentrations of total dissolved solids (TDS), calcium (Ca), magnesium (Mg), sodiu

(K), carbonate alkalinity (CA), sulfate, chl;oride (Cl), fluoride (F), silicon (Si) and dissolved organic carbon in and Kuparuk rivers during peak discharge in June 2002. 

River Cond. (μS) TDS (μeq/L) Ca (μeq/L) Mg (μeq/L) Na (μeq/L) K (μeq/L) CA (μeq/L) Sulfate (μeq/L) Cl (μeq/L) F (μeq/L) 

Peak Discharge 

Sagavanirktok 

(n = 26) 

Mean 

Std. Dev. 

Range 

222 

± 27 

153-

249 

4250 

± 640 

3020-

4980 

1640 

± 204 

1210-1850

450 

± 96 

260-530

44 

± 8 

25-51

8.5 

± 4 

5-17 

1590 

± 215 

1190-1880 

498 

± 142 

259-663

22.1 

± 13.7 

9-52 

7 

± 4 

2-16 

Kuparuk 

(n = 19) 

Mean 

Std. Dev. 

Range 

102 

± 23 

56-132 

2030 

± 480 

1470-

2550 

836 

± 212 

410-1010

135 

± 25 

100-163

50 

± 16 

38-70

14.4 

± 6.2 

7-29 

907 

± 245 

380-1180 

16.2 

± 11 

9-33 

71.5 

± 23.2 

40-131 

2 

± 1 

1-4 
50

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

(mglL)

0

2

4

6

8

10

20

30

40

Calcium

Magnesium

Sulfate 

Sagavanirktok R. (2002)

 

6/1/2001 6/8/2001 6/15/2001 6/22/2001 mg/L

0

2

4

6

8

10

20

30

40

50

Magnesium

Calcium 

Sulfate 

Sagavanirktok R. (2001)

6/1/2001 6/8/2001 6/15/2001 6/22/2001

mg/L

0

1

2

5

10

15

20

Calcium 

Magnesium 

Kuparuk R. (2001)

Figure 3-21. Concentrations of dissolved calcium, magnesium and sulfate in the Sagavanirktok and 

Kuparuk rivers during June 2002 and 2001. Concentrations of sulfate in the Kuparuk 

River were below detection limits in 2001. 

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

(mg/L)

0.0

0.5

1.0

1.5

2.0

2.5

10.0

15.0

20.0

25.0

Calcium

Magnesium

Sulfate 

Kuparuk R. (2002) 
51

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

K (mg/L)

0.0

0.5

1.0

Sagavanirktok 2002

Kuparuk 2002

Figure 3-22. Concentrations of dissolved potassium (K) in the Sagavanirktok and Kuparuk 

rivers during June 2002. 

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

DOC (mg/l)

0

2

4

6

8

10

12

14 Sagavanirktok 2002

Kuparuk 2002 

Figure 3-23. Concentrations of dissolved organic carbon (DOC) in the Sagavanirktok and 

Kuparuk rivers during June 2002. 
52

3.2.3 Dissolved Trace Metals and Dissolved Organic Carbon 

Concentrations of Cd, Cu, Fe, Mn, Pb and Zn in the Sagavanirktok River were higher during the 

peak flow for 2002 relative to off-peak levels in June 2002 (Table 3-11 and Figures 3-24 and 3-

25). However, the mean and maximum concentrations of dissolved Ba, Cu, Fe, Pb and Zn in the 

Sagavanirktok River during May-June 2002 were lower than observed during 2001 (Table 3-11). 

As described in the previous section, this trend is most likely related to the unusual flow pattern 

and lower levels of DOC during the spring 2002 flood in the Sagavanirktok River. 

In the Kuparuk River, the peak in concentrations of K and DOC during peak flow (Figures 3-22 

and 3-23) coincided with peak levels of Cu, Fe and Mn (Figure 3-24). However, with the 

exception of Ba, the same trend of lower levels of metals during 2002 versus 2001 also was 

observed for the Kuparuk River, most likely because of the lower levels of DOC in the 2002 

rather than a difference in the flow pattern. 

Overall, concentrations of Fe and K from the Sagavanirktok and Kuparuk Rivers for both 2001 

and 2002 were directly related to concentrations of DOC (Figure 3-26). Release of soil nutrients 

and metals during the early stages of the spring thaw and flood event, combined with 

complexation of metals by DOC, help explain these observations. 
53

Table 3-11. Concentrations of dissolved metals and dissolved organic carbon (DOC) and total suspended 

Sagavanirktok, Kuparuk and Colville rivers during peak discharge in 2002 and 2001. 

River Ba (μg/L) Cu (μg/L) Fe (μg/L) Pb (ng/L) Zn (μg/L) D

(m

Sagavanirktok 2002 (n = 23) 

Mean Std. Dev. Range 

29.9 

± 2.1 

25.8-33.5 

0.34 

± 0.16 

0.06-0.59 

31 

± 29 

4.0-101 

17 

± 10 

6-40 

0.22 

± 0.17 

0.03-0.63 

5

± 

2.7

Kuparuk 2002 (n = 13) 

Mean Std. Dev. Range 

26.4 

± 3.9 

18-31.8 

0.28 

± 0.12 

0.15-0.56 

81 

± 51 

17-171 

30 

± 13 

16-66 

0.29 

± 0.15 

0.11-0.64 

9

± 

6.1

Sagavanirktok 2001 (n = 11) 

Mean Std. Dev. Range 

31.8 

± 2 

27.5-35.1 

0.79 

± 0.5 

0.57-0.96 

38.1 

± 24.0 

11.2-72.0 

27.8 

± 12.6 

15.5-46.6 

0.22 

± 0.11 

0.13-0.44 

5

± 

2.0

Kuparuk 2001 (n = 5) 

Mean Std. Dev. Range 

19.5 

± 1.5 

18.0-21.0 

0.80 

± 0.08 

0.72-0.86 

212 

± 27 

181-232 

53.0 

± 0.8 

52.4-53.9 

0.38 

± 0.3 

0.36-0.41 

1

± 

12.6

Colville 2001 (n = 3) 

Mean Std. Dev. Range 

50.7 

± 3.6 

46.7-53.8 

2.5 

± 0.2 

2.2-2.7 

80.9 

± 29.9 

59.9-102 

60.1 

± 9.3 

53.5-66.5 

0.14 

± 0.02 

0.11-0.17 

1

± 

8.0
54

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Ba (

μg/L)

15

20

25

30

35

40

Sagavanirktok 2002

Kuparuk 2002 

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Cd (ng/L)

0

20

40

60

80

100

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Cu (

μg/L)

0.0

0.2

0.4

0.6

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Fe (

μg/L)

0

50

100

150

200

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Mn (

μg/L)

0

5

10

15

20

25

30

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Ni (

μg/L)

0.0

0.2

0.4

0.6

0.8

1.0

1.2

Figure 3-24. Concentrations of dissolved barium (Ba), cadmium (Cd), copper (Cu), iron (Fe), 

manganese (Mn) and nickel (Ni) in the Sagavanirktok and Kuparuk rivers during June 

2002. 
55

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Pb (ng/l)

0

20

40

60

80

Sagavanirktok 2002

Kuparuk 2002

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Zn (

μg/l)

0.0

0.2

0.4

0.6

Figure 3-25. Concentrations of dissolved lead (Pb) and zinc (Zn) in the Sagavanirktok and Kuparuk 

rivers during June 2002. 

DOC (mg/L)

0 2 4 6 8 10 12 14 16 18

Fe (

μg/L)

0

50

100

150

200

250

Sagavanirktok 2002

Kuparuk 2002

Sagavanirktok 2001

Kuparuk 2001

DOC (mg/L)

0 2 4 6 8 10 12 14 16 18

K (mg/L)

0.0

0.2

0.4

0.6

0.8

1.0

1.2

1.4

Figure 3-26. Concentrations of dissolved organic carbon (DOC) versus dissolved iron and potassium for 

the Sagavanirktok and Kuparuk rivers for June 2001 and 2002. 
56

3.2.4 Particulate Trace Metals and Organic Carbon 

Mean concentrations of particulate Al, Ba, Cu, Fe, Pb and Zn (μg/g dry weight) for samples 

collected during May-June 2002 were similar (within ±10-20%) to values determined for the 

2001 samples (Table 3-12). In contrast with 2001, concentrations of particulate trace metals and 

Al varied during June with increased concentrations observed when the river slowed down and 

refroze. The slow down led to settling of larger particles and an increase in the fractional 

amounts of fine-grained aluminosilicates. Concentrations of particulate Ba (Figure 3-27) provide 

an example of the observed trend. However, the Ba/Al and other metal/Al ratios did not change 

significantly during June. Once again, concentrations of particulate Ba, Cu, Fe and Zn were 

poorly correlated with organic carbon and relatively well correlated with particulate Al (Table 3-

13). The poor or negative correlations for POC versus Cu, Fe and Zn suggest that POC does not 

play a significant role in controlling concentrations of particulate trace metals in the 

Sagavanirktok River but that the aluminosilicate (clay) content is more important. 

Table 3-12. Concentrations of aluminum, barium, copper, iron, lead, zinc and particulate 

organic carbon (POC) in the Sagavanirktok and Kuparuk rivers during MayJune 2002. 

River Al 

(%) 

Ba 

(μg/g) 

Cu 

(μg/g) 

Fe 

(%) 

Pb 

(μg/g) 

Zn 

(μg/g) 

POC 

(%) 

Sagavanirktok 

 2002 

Mean 

Std. Dev. 

Range

6.2 

± 1.1 

5.0-8.8

698 

± 160 

541-1110

33.3 

± 5.7 

25.6-45.4

3.5 

± 0.6 

2.8-4.7

11.9 

± 4.1 

4.3-23.2

142 

± 31 

116-214

1.6 

± 0.3 

1.2-2.4

Kuparuk 2002 

Peak Discharge 

Mean 

Std. Dev. 

Range 

4.0 

± 1.5 

2.6-7.5 

537 

± 237 

358-1219 

28.4 

± 6.0 

17.6-38.5 

4.5 

± 0.8 

2.7-5.4 

18.9 

± 3.8 

10.3-24.6 

152 

± 62 

81-263 

5.3 

± 3.1 

1.7-10.9 

Sagavanirktok 

 2001 

Mean 

Std. Dev. 

Range

5.6 

± 0.9 

4.0-7.7

702 

± 113 

542-1008

32.8 

± 2.8 

29.7-39.2

3.3 

± 0.4 

2.6-4.0

18.0 

± 2.0 

16.0-23.4

123 

± 7 

115-135

1.6 

± 0.49 

0.7-2.7

Kuparuk 2001 

Peak Discharge 

Mean 

Std. Dev. 

Range 

5.2 

± 0.5 

4.6-5.8 

615 

± 88 

497-743 

32.3 

± 5.8 

25.7-37.2 

3.6 

± 0.2 

3.3-3.8 

15.7 

± 0.7 

14.7-16.6 

124 

± 13 

110-145 

4.6 

± 1.1 

3.3-5.9 
57

5/20/02 5/27/02 6/3/02 6/10/02 6/17/02 6/24/02 

Particulate Ba (

μg/g)

0

300

600

900

1200

Figure 3-27. Concentrations of barium (Ba) for suspended sediment from the Sagavanirktok River for 

May-June 2002. 

Table 3-13. Correlations for particulate trace metals and particulate organic carbon 

(POC) in the Sagavanirktok River during June 2002. 

** Correlation is significant at the 0.01 level. 

 * Correlation is significant at the 0.05 level. 

Al Ba Cu Fe Pb Zn 

Al 1 

Ba 0.58** 1 

Cu 0.91** 0.50* 1 

Fe 0.92** 0.59** 0.88** 1 

Zn 0.90** 0.56* 0.96** 0.91** 0.16 1 

POC -0.39 -0.10 -0.14 -0.52 -0.64** -0.18 
58

3.3 Transport of Dissolved and Particulate Trace Metals and Organic Carbon by Rivers to 

the Coastal Beaufort Sea 

Values for transport of metals and organic carbon by rivers to the coastal Beaufort Sea are 

difficult to calculate due to limitations in flow and chemical data as well as possible 

contributions from summer rainstorms. Nevertheless, by comparing transport during peak 

discharge in June with transport during the remainder of the year, a sense of the relative 

importance of spring floods to annual budgets was obtained. Calculations for material transport 

are presented here for the Kuparuk and Sagavanirktok rivers during 2001 because data for water 

flow are available (U.S.G.S., 2001). 

Water discharge in the Kuparuk River for 2001 was divided into three periods: (1) 0.3 x 1012 L 

(25% of total) during three days of flood discharge in June, (2) 0.4 x 1012 L (33% of total) during 

the 21 off-peak days in June and (3) 0.5 x 1012 L (42% of total) during the remaining 90 days of 

the water year (U.S.G.S., 1971-2001). By combining water flow data with average 

concentrations of DOC for each time period, 42% of the annual load of DOC ([(0.25)(14.0 

mg/L)]/[(0.25)(14.0 μM) + (0.33)(8.7 mg/L) + (0.42)(375 4.5 mg/L)] x100%) from the Kuparuk 

River was delivered to the Beaufort Sea in 3 days. Using the same approach shown above for 

DOC, the following fractions of the annual loads of dissolved metals were carried by the 

Kuparuk River in three days of peak flow: Ba (16%), Cu (36%), Fe (67%), Pb (47%) and Zn 

(46%). 

Using the U.S.G.S. data for the Sagavanirktok River and assuming that it represents discharge 

flow for 20% of the system, then the annual flow can be scaled up and grouped as follows: (1) 

1.0 x 1012 L (17% of total) of peak flow during 12 days in June, (2) 1.2 x 1012 L (18% of total) of 

off-peak flow during 16 days in June and (3) 4.2 x 1012 L (65% of total) during the remaining 90 

days of the water year (U.S.G.S., 1971-2001). Using DOC data, 33% of the annual load of DOC 

[(0.17)(5.8 mg/L)]/[(0.17)(5.8 mg/L) + (0.18)(2.4 mg/L) + (0.65 x 2.4 mg/L)] x 100%) was 

transported to the coastal Beaufort Sea in 12 days. Using the same approach, the fractions of the 

annual transport of dissolved metals carried by the Sagavanirktok River in 12 days were as 

follows: Ba (15%), Cu (38%), Fe (74%), Pb (50%) and Zn (40%). 

Calculations for annual transport of elements with suspended sediment are based on two time 

periods (1) peak flow and (2) off-peak flow in June plus the remainder of the summer, because 

sediment transport was predominantly during peak flow and because differences in 

concentrations of elements in the particulate form (on a dry weight basis) varied only slightly 

among time periods. During the three days of peak water flow in the Kuparuk River in June 

2001, TSS averaged 63 mg/L to yield a sediment discharge of ~19,000 t. During the off-peak 

period in June and the remainder of the summer, TSS values averaged 4 and ~0.5 mg/L, 

respectively, resulting in an additional total of 1,900 t of sediment discharged. Thus, >90% of 

the annual transport of particulate Pb occurred during peak flow in the Kuparuk River during 

three days ([(0.90)(15.7 μg/g)] /[(0.10)(14.4 μg/g) + (0.90)(15.7 μg/g)] x 100%). Using the same 

approach, >89% of the other particulate metals and POC were transported to the coastal Beaufort 

Sea by the Kuparuk River in 3 days. 
59

For the Sagavanirktok River, TSS averaged 267 mg/L during peak discharge in June to yield 

267,000 t of sediment during the 12-day peak period. Concentrations of TSS averaged 31 and 

1.3 mg/L during the off-peak period in June and the remainder of the summer, respectively, 

transporting an additional 36,000 t of sediment to the coastal Beaufort Sea. Particulate metal 

concentrations in the Sagavanirktok River did not vary greatly during peak and off-peak periods 

(Table 3-12) and therefore, >88% of particulate Pb, the other metals and POC were transported 

during the 12 days of peak discharge ([0.88)(18.3 μg/g)]/[(0.12)(18.3 μg/g) + (0.88)(18.3 μg/g] x 

100%). 

Results from this study also provide a direct comparison of the relative abundances of dissolved 

and particulate forms of metals and organic carbon in the arctic rivers of Alaska. During the 

brief periods of peak flow, the dissolved fraction accounted for 57% ([5.8 mg/L]/[(5.8 mg/L) + 

(16 mg/g/0.267 g/L) x 100%]) and 83% of DOC transport in the Sagavanirktok and Kuparuk 

rivers, respectively (Table 3-14). When combined with the off-peak data, the results indicate 

that DOC was dominant form of OC discharged to the coastal Beaufort Sea from these Alaskan 

arctic rivers. Dissolved Ba accounted for >14% of total Ba transport during peak flow and at 

least 59% of Ba transport during off-peak flow in June (Table 3-14). In the Sagavanirktok River, 

<3% of the total Fe, Pb and Zn were in the dissolved phase during both peak and off-peak 

periods, whereas dissolved Cu was ≥9% of the total Cu, possibly due to complexation by DOC 

(Cabaniss and Shuman, 1998). 

Table 3-14. Percentage of trace metals and organic carbon in the dissolved phase during peak and 

off-peak discharge in the Sagavanirktok and Kuparuk rivers. 

Ba Cu Fe Pb Zn OC 

Sagavanirktok River 

Dissolved (%) Peak 14 9 0.5 0.6 0.7 57 

Dissolved (%) Off-peak 59 29 0.6 2 3 83 

Kuparuk River

Dissolved (%) Peak 33 28 9 5 4.6 83 

Dissolved (%) Off-peak 93 87 30 41 44 98 
60

3.4 Partitioning of Metals between Dissolved and Particulate Phases in Rivers 

The chemical forms of metals in rivers are an important starting point for understanding their 

subsequent behavior in the saline water of the coastal Beaufort Sea. Concentrations of dissolved 

and particulate Ba varied by a factor of 2 to 3 among rivers (Figure 3-28). However, 

concentrations of dissolved Ba varied in proportion to concentrations of particulate Ba (Figure 3-

28). Therefore, distribution coefficients (Kd) were used to model the behavior of dissolved and 

particulate Ba during the spring discharge and summer samples. Distribution coefficients 

provide a measure of partitioning between dissolved and particulate phases and were calculated 

in this study using 

(concentration of particulate metal in μg metal/g particles) 

Kd = _________________________________________________________________________ . 

 (concentration of dissolved metal in μg metal/g water) 

where the conceptual perspective is shown below by considering that dissolved Ba2+ can adsorb 

and desorb from suspended particles in a predictable manner. 

 

Despite significant differences in concentrations of dissolved and particulate Ba among rivers, 

the Kd values calculated for Ba were statistically equal (t-test, α = 0.05), with the following 

average for samples collected during June, July and August; 2.3 ± 0.3 x 104

 (average log 

Kd = 4.36) in the Sagavanirktok River, 2.6 ± 0.5 x 104 in the Kuparuk River and 2.1 ± 0.4 x 104 in 

the Colville River (Figure 3-28). These results suggest that partitioning of Ba between dissolved 

and particulate phases is an equilibrium controlled process between free Ba2+ and suspended 

particles. Considering the large variations in water discharge, TSS, and concentrations of 

organic carbon, the apparent uniformity of the distribution coefficients for Ba indicates that 

discharge, TSS and organic carbon have little impact on the partitioning of Ba between dissolved 

and particulate phases. 

The broader implication of these results for the biogeochemistry of Ba in rivers is potentially 

important. Do concentrations of particulate and dissolved Ba in other rivers follow similar 

behavior? Unfortunately, investigators have seldom determined both particulate and dissolved 

Ba concentrations for the same sample in rivers and the only data identified to date are for 

concentrations of particulate and dissolved Ba from another northern Alaskan River, the 

Kuskokwim River (Wang, 1999). The average Kd based on 5 samples was 2.6 ± 0.6 x 104

. 

These preliminary results suggest that differences between the North American and Eurasian 

concentrations for dissolved Ba, such as those found by Guay and Falkner (1998) are linked to 

geology by being dependent upon the Ba concentrations of river particles. 

+ Ba2+ Ba2+
61

Dissolved (nM) Particulate (μg/g) x

Ba

0

200

400

600

800

1000

1200

Sagavanirktok

Kuparuk

Colville

2001

Kd (x100)

Dissolved (nM) Kd (x 100)

Ba

0

200

400

600

800

1000

1200

Sagavanirktok

Kuparuk

Particulate (μg/g)

2002

Figure 3-28. Average concentrations of dissolved and particulate barium (Ba) and distribution 

coefficients (Kd) for Ba in the Sagavanirktok, Kuparuk and Colville rivers. 
62

The combined effect of significantly increased concentrations of dissolved Cu, Pb (Figure 3-29) 

and Zn during peak discharge with relatively constant concentrations of particulate metals 

suggest that a Kd is less likely to explain dissolved concentrations of these metals. During peak 

discharge, Kd values (x 104

) for Cu (4.4), Pb (116) and Zn (67) were 40 to 50% lower than 

during off-peak discharge in the Sagavanirktok River. In contrast, concentrations of DOC were 

~40% greater during peak discharge. Strong correlations between dissolved metals and DOC 

suggest that elevated concentrations of organic ligands during peak discharge alter partitioning of 

Cu, Pb and Zn between dissolved and particulate phases. Thus, Kd values, are potentially more 

useful in low DOC riverine environments. Results from previous studies in rivers have shown 

that distribution coefficients for Cu, Pb and Zn often have order-of-magnitude differences where 

a large fraction of the variance can be explained by concentrations of DOC (Shafer et al., 1999). 

 

Figure 3-29. Concentrations of dissolved and particulate lead (Pb) in the Sagavanirktok, Kuparuk and 

Colville Rivers during summer 2001 and log Kd for Pb. Results for the Mississippi River 

(Miss) are presented for comparison (Trefry et al., 1986). Scaling for Kd is as log Kd, so log 

Kd = 6 is the same as Kd = 100 x 104

. 

Sag Kup Col Miss

0

50

100

150

200

Dissolved Pb(ng/L)

14 ± 5

47 ± 17

Sag Kup Col Miss

0

10

20

30

40

Particulate Pb (μg/g)

Sag Kup Col Miss

0

2

4

6

8

log Kd for Pb
63

3.5 Dissolved and Particulate Metals in the Coastal Beaufort Sea 

Concentrations of dissolved As, Ba, Cd, Cr, Cu, Hg, Pb and Zn (Tables 3-15, 3-16 and 3-17) 

were determined for samples of saline water from the coastal Beaufort Sea. Concentrations of 

these elements were markedly lower than pertinent freshwater or salt water criteria established 

by the U.S. EPA (Table 3-18). Concentrations of total Hg in the coastal Beaufort Sea also were 

low at about 0.5-0.8 ng/L, relative to levels of ~2 ng/L in the source rivers; all of which were 

well below established water quality criteria. With respect to dissolved trace metals, area rivers 

and coastal seawater are pristine. We also determined concentrations of selected metals in 

samples of snow collected during 2002 at inland and offshore locations (Table 3-18). The 

concentrations of metals in snow were generally about 10 times lower than average values in the 

rivers and lower than values for river water during pre-peak flow. 

A schematic look at concentrations of dissolved As (Figure 3-30) shows a progressive increase in 

concentrations from low levels in rivers to about 10 times higher levels in coastal seawater. This 

trend is typical for As and results from a combination of limited sources in crustal rocks and a 

relatively long residence time in seawater (~40,000 years, Broecker and Pang, 1984). 
64

Table 3-15. Means and standard deviations (SD) for salinity, total suspended solids (TSS), and concentrations o

dissolved organic carbon (DOC) for water collected from the coastal Beaufort Sea during August 20

2000 Station Grouping 

Salinity 

(psu) 

TSS 

(mg/L) 

As 

(μg/L) 

Ba 

(μg/L) 

Cd 

(μg/L) 

Cr 

(μg/L) 

Cu 

(μg/L) 

Hg 

(ng/L) 

Pb 

(ng/L) 

Zn 

(μg/L) 

North Star Area (n=2) 

Mean ± SD 

22 

±4 

7.3 

±4.0 

0.55 

±0.02 

29 

±0.1 

0.018 

±0.001 

0.055 

±0.005 

0.57 

±0.02 

0.4 

±0.10 

5 

±1 

0.13 

±0.02 

Liberty Area (n=2) 

Mean ± SD 

22 

±0.2 

10.3 

±1.6 

0.54 

±0.13 

20 

±1 

0.025 

±0.004 

0.081 

±0.06 

0.53 

±0.03 

0.9 

±0.1 

5 

±2 

0.24 

±0.00 

Beaufort Sea Monitoring Program (n=2) 

Mean ± SD 

21 

±2 

9.9 

±7.3 

0.37 

±0.01 

32 

±1 

0.017 

±0.001 

0.059 

±0.002 

0.53 

±0.01 

0.4 

±0.1 

5 

±1 

0.22 

±0.06 

Cumulative. (n=6) 

Mean ± SD 

22 

±3 

8.2 

±4.8 

0.49 

±0.11 

27 

±6 

0.020 

±0.004 

0.065 

±0.013 

0.54 

±0.03 

0.5 

±0.3 

5 

±1 

0.20 

±0.06 
65

Table 3-16. Means and standard deviations (SD) for salinity, total suspended solids (TSS), and concentrations 

dissolved organic carbon (DOC) for water collected from the coastal Beaufort Sea during August 20

2001 Station Grouping 

Salinity 

(psu) 

TSS 

(mg/L) 

As 

(μg/L) 

Ba 

(μg/L) 

Cd 

(μg/L) 

Cr 

(μg/L) 

Cu 

(μg/L) 

Hg 

(ng/L) 

Pb 

(ng/L) 

Z

(μg

North Star Area (n=5) 

Mean ± SD 

18 

±5 

3.9 

±1.8 

0.43 

±0.16 

34 

±10 

0.019 

±0.003 

0.10 

±0.03 

0.66 

±0.10 

1.3 

±0.3 

6 

±3 

0

±0

Liberty Area (n=2) 

Mean ± SD 

14 

±2 

6.7 

±1.2 

0.34 

±0.04 

28 

±0.4 

0.023 

±0.004 

0.10 

±0.02 

0.57 

±0.12 

- - 

22 

±7 

0

±0

Beaufort Sea Monitoring Program (n=4) 

Mean ± SD 

16 

±4 

5.5 

±2.3 

0.33 

±0.12 

32 

±7 

0.023 

±0.007 

0.08 

±0.01 

0.64 

±0.04 

- - 

8 

±3 

0

±0

Cumulative. (n=11) 

Mean ± SD 

17 

±4 

5.0 

±2.2 

0.38 

±0.13 

32 

±8 

0.021 

±0.005 

0.09 

±0.02 

0.64 

±0.08 

- - 

10 

±7 

0

±0
66

Table 3-17. Means and standard deviations (SD) for salinity, total suspended solids (TSS), and conce

metals and dissolved organic carbon (DOC) for water collected from the coastal Beaufo

2002. 

2002 Station Grouping 

Salinity 

(psu) 

TSS 

(mg/L) 

As 

(μg/L) 

Ba 

(μg/L) 

Cd 

(μg/L) 

Cu 

(μg/L) 

Hg 

(ng/L) 

Pb 

(ng/L) 

Zn 

(μg/L) 

North Star Area (n=11) Mean ± SD 22 ±4 2.5 ±1.5 0.49 ±0.17 15 ±3 0.026 ±0.004 0.44 ±0.16 2.0 (n=1) 7 ±2 0.12 ±0.10 Beaufort Sea Monitoring Program (n=21) 

Mean ± SD 

20 

±4 

1.9 

±1.2 

0.52 

±0.13 

14 

±2 

0.028 

±0.005 

0.48 

±0.07 

0.6 

±0.3 

(n=4) 

7 

±3 

0.11 

±0.05 

Cumulative (n=32) 

Mean ± SD 20 ±5 2.1 ±1.3 0.51 ±0.14 14 ±2 0.027 ±0.005 0.47 ±0.11 0.9 ±0.7 (N=5) 7 ±3 0.11 ±0.07 
67

Table 3-18. Concentrations of selected dissolved metals (0.4 μm filtered) in snow, Sagavanirktok River 

water and Beaufort Sea water compared with U.S. EPA criteria for freshwater and 

saltwater. 

Concentrations of Dissolved Metals

(ng/L or parts per trillion)

As Ba Cu Pb

Terrestrial Snow 9 750 58 7

Marine Snow 33 570 70 -

Sagavanirktok River 130 32,000 590 21

Coastal Beaufort Sea 1200 12,000 650 7

Federal Fresh Water

Quality Criteria 150,000 1 x 106 9000 2500

Federal Salt Water

Quality Criteria 36,000 1 x 106 3100 8100

Rivers

Coastal Beaufort Sea Coastal Beaufort Sea

0.1 μg/L 0.1 μg/L

Dissolved As Dissolved As

0.9-1.3 μg/L 1.3 μg/L @ Salinity ~ 30 @ Salinity ~ 30 psu

~0.4-0.7 μg/L @ Salinity ~20 @ Salinity ~20 psu

~0.2-0.4 μg/L 0.4 μg/L @ Salinity ~10 @ Salinity ~10 psu

Figure 3-30. Generalized distribution of dissolved arsenic (As) in source rivers and coastal water of the 

Beaufort Sea. 
68

The schematic look at the concentrations and cycling of As in Figure 3-30 is presented as 

concentrations of As in snow, river water, and summer seawater versus salinity in Figure 3-31. 

If a simple mixing curve is developed between the river water and highest salinity offshore 

water, concentrations of As during summer at mid-salinities were lower than predicted by the 

spring mixing curve. The apparent removal of As may be due to biological uptake or scavenging 

by iron oxides or clays. 

Figure 3-31. Concentrations of dissolved arsenic (As) versus salinity (practical salinity units) where 

values for snow and river water plot close to the zero points of the graph relative to 

summer seawater (circles). Line shows straight line mixing curve for river water and 

saline water from the Beaufort Sea. 

In contrast with As, concentrations of Ba were about 3 times higher in the open, saline water of 

the Beaufort Sea relative to the source rivers (Figure 3-32). Furthermore, Figure 3-32 shows the 

characteristic desorption of Ba from particles during freshwater-seawater mixing. 

Concentrations of Ba were about 50 times lower in snow than river water (Figure 3-33). As river 

water mixes with seawater at low salinity (<10 psu) Ba desorbs from river-borne particles due to 

increasing concentrations of competing cations. Then, concentrations of Ba generally follow 

simple mixing with increasing salinities. 

Salinity (psu)

0 10 20 30 40

Dissolved As (

μg/L)

0.0

0.2

0.4

0.6

0.8

1.0

1.2

1.4

2002

2000 

2001

Snow

River water
69

Rivers

Coastal Beaufort Sea Coastal Beaufort Sea

30 μg/L 30 μg/L

Dissolved Dissolved Ba

~10 μg/L ~10 μg/L @ Salinity ~ 30 @ Salinity ~ 30 psu

30- 50 μg/L @ Salinity ~ 10 @ Salinity ~ 10 psu

Figure 3-32. Generalized distribution of dissolved barium (Ba) in source rivers and coastal water 

of the Beaufort Sea. 

Figure 3-33. Concentrations of dissolved barium (Ba) versus salinity (practical salinity units) where 

values for snow and river water plot close to zero salinity relative to values for summer 

seawater (circles). Line shows straight line mixing curve for river water and saline water 

from the Beaufort Sea. 

 

Salinity (psu)

0 10 20 30 40 50

Dissolved Ba (

μg/L)

0

10

20

30

40

50

60

2002 

2000 

2001

Snow

River Water
70

3.6 Dissolved and Particulate Organic Substances in Seawater 

The Total PAH (TPAH) concentrations in the whole seawater samples (dissolved + particulate 

fractions) were low and ranged from 22 to 68 ng/L (parts per trillion in Table 3-19). The TPAH 

of the particulate fraction of the seawater samples ranged from 21.1 to 54.8 ng/L and the 

concentration in the dissolved fractions ranged from 13.2 to 18.5 ng/L (Table 3-19). The PAH 

distributions of the particulate seawater samples were very similar suggesting a similar source of 

hydrocarbons in all samples. Examples of representative BSMP and Northstar station PAH 

distribution histograms are presented in Figure 3-34. The PAH distribution of the particulates 

shows a petrogenic or petroleum hydrocarbon composition, characterized by a predominance of 

the 2- and 3-ringed alkyated PAH compounds, with a lower abundance of 4-, 5-, and 6-ringed 

PAH. One exception is phenanthrene, the most abundant individual PAH detected in the 

samples, and to a lesser degree naphthalene and C1-phenanthrenes. However, these three 

analytes also were detected in the procedural blank at comparable concentrations, indicating that 

the observed abundances of these analytes are laboratory artifacts. In general, the PAH 

distribution of the particulate fractions is similar to the pattern observed in the river sediment and 

surface benthic sediment from the region (Brown et al., 2003). The dissolved phase of the water 

samples had only trace level concentrations and both the PAH levels and distributions were 

similar to the associated laboratory procedural blank. Based on these results, and accounting for 

the procedural blank PAH concentrations, PAH concentrations in the dissolved phase of the 

samples were below detection limits. 

A t-test procedure was used to determine if any key PAH parameters (Table 3-19) were 

significantly different between the water samples collected at Northstar stations (n = 4) and at 

BSMP/Liberty stations (n = 4). The BSMP station 5A is located within 3 Km of the Northstar 

Island and thus was included as a Northstar region station for the statistical analyses. 

Concentration variables were log-transformed prior to analysis to normalize the distributions. 

No significant differences were found between the Northstar stations and the BSMP/Liberty 

stations. Partition coefficients were not calculated for the individual PAH compounds in the 

Beaufort Sea seawater samples due to the majority of trace and non-detect values reported for the 

dissolved fraction. 

Overall, the results of the Beaufort Sea seawater organic analyses show low levels of PAH with a 

composition generally similar to the riverine and benthic sediment of the region. The PAH in the 

seawater samples are primarily associated with the suspended sediment in the particulate 

fraction. The analyses of the dissolved fraction show no appreciable PAH in the dissolved phase 

(after comparison to laboratory blank levels), indicating that the PAH are tightly bound to the 

suspended particulate matrix and do not readily partition into the dissolved phase. 
71

Table 3-19. Summary data for polycyclic aromatic hydrocarbons (PAH) in Beaufort Sea water samples 

Station Sample Type Units Total PAH 2-Ring PAH 3-Ring 

PAH 

4-Ring 

PAH 

5+-Ring PAH 

Filter Samples 

3A Particulate ng/L 22.0 8.38 8.48 3.32 1.85 

4A Particulate ng/L 40.8 20.0 11.0 6.59 3.13 

5A Particulate ng/L 32.7 12.9 10.5 7.91 1.42 

L08 Particulate ng/L 48.4 21.8 12.0 10.5 4.09 

L12 Particulate ng/L 54.8 16.4 20.5 15.4 2.59 

N01 Particulate ng/L 21.1 7.54 7.68 4.64 1.21 

N10 Particulate ng/L 40.7 15.4 13.6 8.50 3.25 

N13 Particulate ng/L 38.8 16.2 11.7 8.13 2.80 

Blank Particulate ng/L 9.86 6.13 2.93 0.80 0.00 

Filtered Water Samples 

3A Dissolved ng/L 16.9 14.6 1.30 0.93 0.07 

4A Dissolved ng/L 13.2 10.6 1.30 1.25 0.09 

5A Dissolved ng/L 14.7 13.2 0.96 0.60 0.00 

L08 Dissolved ng/L 14.4 11.8 1.40 1.13 0.06 

L12 Dissolved ng/L 17.7 14.6 1.80 1.28 0.08 

N01 Dissolved ng/L 18.5 16.4 1.22 0.87 0.00 

N10 Dissolved ng/L 15.9 14.0 1.13 0.73 0.00 

N13 Dissolved ng/L 16.1 13.9 1.45 0.74 0.00 

Blank Dissolved ng/L 12.7 10.2 1.72 0.75 0.00 

Whole Water Samples 

3A Whole Water ng/L 37.6 22.5 9.26 4.05 1.80 

4A Whole Water ng/L 50.8 29.1 11.5 7.33 2.98 

5A Whole Water ng/L 45.4 25.3 10.8 8.02 1.33 

L08 Whole Water ng/L 59.0 31.9 12.5 10.8 3.83 

L12 Whole Water ng/L 68.5 29.7 20.8 15.5 2.47 

N01 Whole Water ng/L 40.1 24.1 9.09 5.62 1.24 

N10 Whole Water ng/L 54.0 28.5 13.8 8.67 3.03 

N13 Whole Water ng/L 52.6 29.1 12.4 8.37 2.63 

Blank Whole Water ng/L 22.6 16.4 4.65 1.55 0.00 
72

Figure 3-34. Distribution histogram for polycyclic aromatic hydrocarbons (PAH) in Beaufort Sea 

seawater samples 3A-01 and N01-01 – particulate fraction. 

 Sample 3A-01- Particulate Fraction

0

0.5

1

1.5

2

2.5

3

3.5

4

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)

 Sample N01-01- Particulate Fraction

0.00

0.50

1.00

1.50

2.00

2.50

3.00

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)
73

Figure 3-35. Distribution histogram for polycyclic aromatic hydrocarbons PAH) in Beaufort Sea 

seawater samples 3A-01 and procedural blank – dissolved fraction. 

 Sample 3A-01- Dissolved Fraction

0

1

2

3

4

5

6

7

8

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)

 Procedural Blank - Dissolved Fraction

0.00

1.00

2.00

3.00

4.00

5.00

6.00

7.00

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)
74

3.7 Spike Study for Polycyclic Aromatic Hydrocarbons 

The primary purpose of the Spike Study was to determine equilibrium kinetics for release and 

uptake of selected organic substances during sediment resuspension events. The PAH 

concentration data from the dissolved and particulate phases will be evaluated to determine the 

degree of uptake or release of crude oil PAH components from particles. These data will serve 

as a baseline for future oil spill modeling, and will provide information on the dissolved phase 

PAH, potential particulate sorption of PAH, and subsequent re-deposition as would be the case in 

an open water oil spill in “storm conditions” in the nearshore Beaufort Sea. 

The TPAH concentration of the whole water samples in spike study was quite variable and 

ranged from 39,700 to 145,000 ng/L. The TPAH concentration in the dissolved fraction 

(equivalent to a water accommodated fraction – WAF) of spike study samples ranged from 

23,500 to 71,300 ng/L and the TPAH concentration in the particulate spike study samples ranged 

from 970 to 80,200 ng/L (Table 3-20). The high degree of variability seen in the particulate 

sample concentrations was likely due to particulate oil or micro-emulsion oil droplets becoming 

entrained in the water phase of some samples during the mixing phase of the study. Despite the 

variability in the particulate sample concentrations, the PAH distributions were very similar for 

the seven replicate samples, and as expected, are similar to the North Slope Crude oil used to 

dose the samples with a predominance of 2- and 3- ringed alkyl PAH and lower levels of 

alkylated 4-ring PAH (Figures 3-36 and 3-37). The PAH distributions of the dissolved sample 

replicates were also similar to each other. However, the PAH distributions in these samples 

(Figure 3-36) is more representative of a WAF, and shows a preferential enrichment of the more 

water soluble 2-ringed PAH (i.e., naphthalene > C1-naphthalenes > C2-napththalenes > C3-

naphthalenes > C4- naphthalenes) and substantially lower levels of the less soluble 3-ring PAH 

(flourenes, phenanthrenes, and dibenzothiophenes) and trace level or non-detects for the 4-, 5-, 

and 6-ring PAH. 

Partition coefficients were not calculated for the individual PAH compounds in the spiked 

Beaufort Sea seawater samples due to the high degree of variability observed in the particulate 

sample concentrations. However, the total PAH concentrations of the whole water samples are 

generally within the range of WAF samples prepared from crude oil and diesel (Hokstad, et al., 

1999; Neff, et al., 2000). It should be noted that the whole water samples from the spike study 

include a substantial amount of suspended sediment (~95 mg/L) which is not normally included 

in the preparation of WAFs. The dissolved fraction of the spike study samples are probably 

more representative of a typical WAF preparation and the TPAH concentrations of the dissolved 

fraction are substantially lower than those reported by Neff et al., 2000 for crude oil, condensate 

and diesel. The lower PAH concentrations observed in the spike study are likely due to the 

lower solubility of the PAH at 4°C versus room temperature (20°C), which is typical for WAF 

preparation in other studies. 
75

Table 3-20. Data summary for polycyclic aromatic hydrocarbons (PAH) in Beaufort Sea spike water study.

Station Spiked With Sample Type Units Total PAH 2-Ring PAH 3-Ring PAH 4-Rin

Filter Samples 

3A-01 None Particulate ng/L 22.0 8.38 8.48 33A-02 Oil and Sediment Particulate ng/L 4450 1990 2050 33A-03 Oil and Sediment Particulate ng/L 5080 2160 2400 53A-04 Oil and Sediment Particulate ng/L 76600 38400 31600 643A-05 Oil and Sediment Particulate ng/L 972 324 512 13A-06 Oil and Sediment Particulate ng/L 36600 17200 15900 343A-07 Oil and Sediment Particulate ng/L 6450 3140 2740 53A-08 Oil and Sediment Particulate ng/L 80200 38000 35000 70

Blank Sediment only Particulate ng/L 79.1 27.3 25.3 1

Filtered Water Samples 

3A-01 None Dissolved ng/L 16.9 14.7 1.30 03A-02 Oil and Sediment Dissolved ng/L 35200 32900 2270 73A-03 Oil and Sediment Dissolved ng/L 40400 37100 3160 13A-04 Oil and Sediment Dissolved ng/L 48800 44100 4510 13A-05 Oil and Sediment Dissolved ng/L 34700 32100 2460 83A-06 Oil and Sediment Dissolved ng/L 71300 65000 6140 13A-07 Oil and Sediment Dissolved ng/L 23500 21900 1550 53A-08 Oil and Sediment Dissolved ng/L 65200 58300 6670 2

Blank Sediment only Dissolved ng/L 44.2 26.9 14.6 2

Whole Water Samples 

3A-01 None Whole water ng/L 37.6 22.5 9.26 43A-02 Oil and Sediment Whole water ng/L 39700 34900 4320 43A-03 Oil and Sediment Whole water ng/L 45500 39200 5560 63A-04 Oil and Sediment Whole water ng/L 125000 82500 36100 663A-05 Oil and Sediment Whole water ng/L 35600 32400 2970 23A-06 Oil and Sediment Whole water ng/L 109000 82200 22000 363A-07 Oil and Sediment Whole water ng/L 30000 25100 4290 63A-08 Oil and Sediment Whole water ng/L 145000 96400 41700 72

Blank Sediment only Whole water ng/L 123 54.2 39.8 1

Spiking Sediment and Oil 

N231 Sediment ng/0.36g 195 60.8 59.7 4

North Slope Crude2 Oil ng/200 mg 2780000 1720000 894000 162

Note1 – 360 mg (dry weight) of N23 sediment was used for spiking samples. Note2 – 200 mg of North Slope Crude was used for spiking samples. 
76

Figure 36. Distribution histogram for polycyclic aromatic hydrocarbons (PAH) in spiked sample 

3A-02 – particulate and dissolved fractions. 

 Sample 3A-02- Particulate Fraction

0

100

200

300

400

500

600

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)

 Sample 3A-02- Dissolved Fraction

0

2000

4000

6000

8000

10000

12000

14000

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/L)
77

Figure 37. Distribution histogram for polycyclic aromatic hydrocarbons (PAH) in spiking 

sediment and oil. 

Spiking Sediment - N23

0

10

20

30

40

50

60

70

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/g)

Spiking Oil - North Slope Crude

0

500

1000

1500

2000

2500

C0NC1NC2NC3NC4N

ACEY

ACE

BIP

C0FC1FC2FC3F

C0AC0P

C1P/AC2P/AC3P/AC4P/A

C0DC1DC2DC3D

FL

PYR

C1F/PC2F/PC3F/P

BAA

C0CC1CC2CC3CC4C

BBFBKF

BEPBAP

PER

INDPYR

DAHA

BGHIP

Concentration (ng/mg)
78

4.0 Summary and Conclusions

Water flow during the three- and 12 day spring flooding events in the Kuparuk and 

Sagavanirktok rivers during June 2001 accounted for ~17% and ~25%, respectively, of 

the annual discharge of water (U.S.G.S., 1971-2001). High-resolution sampling of the 

Sagavanirktok River during peak flow revealed that concentrations of dissolved Cu, Fe, 

Pb, Zn and organic carbon increased by 2 to 25 fold at maximum discharge. Strong 

positive correlations for concentrations of dissolved metals versus DOC suggest that soil 

interstitial water and surface water that were flushed from the drainage basins were 

primary sources of metals and DOC. During off-peak discharge in August, when water 

flow and levels of TSS decreased, concentrations of dissolved metals in the 

Sagavanirktok and Kuparuk rivers were among the lowest values reported for world 

rivers. 

 

Trends in concentrations of dissolved trace metals and organic carbon in the Kuparuk and 

Colville rivers were similar to those observed in the Sagavanirktok River. However, 

concentrations of dissolved metals and DOC were, on average, higher than those 

observed in the Sagavanirktok River during June 2001. These higher concentrations in 

the Kuparuk and Colville rivers appeared to be related to differences in lithology and 

vegetation in the drainage basins. Soils westward of the carbonate rich Sagavanirktok 

River are more acidic. These lower pH soils are likely to support enhanced chemical 

weathering and increased concentrations of dissolved metals and DOC. 

In contrast with Cu, Fe, Pb and Zn, concentrations of dissolved Ba remained relatively 

constant in each river throughout the sampling period with the Sagavanirktok River at 

234 ± 14 nM, the Kuparuk River at 171 ± 16 nM and the Colville River at 376 ± 24nM. 

These data suggest that concentrations of dissolved Ba were not significantly influenced 

by increases in water discharge or concentrations of TSS and DOC. Concentrations of 

dissolved Ba vary in proportion to concentrations of particulate Ba in the Sagavanirktok, 

Kuparuk and Colville rivers. Considering the large range of TSS, water discharge and 

DOC found during this study, we speculate that the fraction of exchangeable fraction of 

Ba associated with the particles may control concentrations of dissolved Ba. 

Concentrations of particulate Cu, Fe, Pb, Zn and OC did not follow the trends observed 

for the dissolved fraction and were relatively constant on a dry weight basis throughout 

the spring floods. In addition, concentrations of particulate metals correlated well with 

particulate Al but were poorly correlated with POC showing that clays rather than 

organic matter control particulate metal concentrations. 

Increases in water discharge during the spring flood events coincided with increased 

concentrations of TSS, dissolved metals, and OC and account for a large fraction of the 

annual transport. In the Kuparuk and Sagavanirktok rivers, >16% of the water flow and 

>80% of the annual sediment discharge occurred during three and 12-day periods, 

respectively. This large pulse of water carried more than one-third of the annual 

dissolved load of Cu, Fe, Pb, Zn and OC and >80% of the particulate metals to a coastal 

Beaufort Sea that was covered with a 2-m thick layer of ice. 
79

Results from analyses of Beaufort Sea seawater show low levels of PAH with a 

composition generally similar to the riverine and benthic sediment of the region. The 

PAH in the seawater samples were primarily associated with the suspended sediment in 

the particulate fraction. The analyses of the dissolved fraction show no appreciable PAH 

in the dissolved phase, indicating that the PAH were tightly bound to the suspended 

particulate matrix and did not readily partition into the dissolved phase. For the spike 

study, the results indicate that while the PAH in the whole water samples from the study 

were comparable to typical WAF PAH levels, the dissolved PAH were substantially 

lower due to the low water temperature used to approximate Beaufort Sea conditions 

during the spike study. 

The main conclusions from ANIMIDA Task 7 are the following: (1) concentrations of 

dissolved trace metals and PAH in the study area are very low and characteristic of 

pristine water, (2) concentrations of some metals can be modeled with a simple 

distribution coefficient, and (3) active physical, chemical and biological processes are at 

work to create a dynamic, yet predictable, distribution of dissolved trace metals. Such 

information will be useful for long-term monitoring of the area (years, decades and 

centuries) and will provide us with an evolving capability for predicting impacts from 

any spills or other releases of chemicals within the drainage basin or coastal sea. 
80

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6.0 Appendices 

The appendices listed below are tabulated on the CD attached to hard copies of this report 

or as separate files on this CD. 

Appendix A: Data for Dissolved and Particulate Metals and Organic Carbon from Rivers 

 for 2001 and 2002 

Appendix B: Chemical Data for Under Ice Samples for 2001 and 2002 

Appendix B1: CTD Under Ice for 2001 

Appendix B2: CTD Under Ice for 2002 

Appendix C: Data for Dissolved and Particulate Metals in the Coastal Beaufort Sea for 

 2000, 2001 and 2002 

 Appendix C1: Aanderaa Data for Summer 1999-2002 

Appendix D: Rember, R.D. (2002) Composition of Dissolved and Suspended Matter 

Transported by the Sagavanirktok, Kuparuk and Colville Rivers in the Alaskan 

Arctic. Ph.D. Dissertation, Florida Institute of Technology, 106 pp. 

Acknowledgements 

We thank the Minerals Management Service (MMS), U.S. Department of Interior, for 

support and encouragement during this project. We especially thank Dick Prentki of 

MMS, the COTR for the study, for his participation in field exercises, for scientific 

consultation, and for his unwavering enthusiasm for ANIMIDA. Support and advice 

from Cleve Cowles, Tom Ahlfeld and Jim Cimato of MMS also are greatly appreciated. 

The Scientific Review Board (SRB) for ANIMIDA played an important and lively role in 

the study and we thank the members of the SRB: Stephan Braund (Stephan Braund & 

Associates), Chris Clark (Cornell University), Ray Jakubczak (British Petroleum), Todd 

O'Hara (North Slope Borough, Department of Wildlife Management) and David Shaw 

(University of Alaska, Fairbanks). In the field, the efforts of Mark Mertz (TEG 

Oceanographic Services, Inc.) as ship captain, Mark Savoie and Gary Lawley (Kinnetic 

Laboratories, Inc.) as physical oceanographers and snow machine leaders, and Michelle 

McElvaine, Mary Sohn and Lee Frey (Florida Institute of Technology) as members of the 

water team, were indispensable and are greatly appreciated. We thank British Petroleum 

(BP) and Arco, now BP-Arco, for logistical support and accommodations throughout the 

project. We thank Phillips Petroleum for helicopter transportation to the Colville River. 

Use of laboratory facilities at the Seawater Treatment Plant (STP) at West Dock and the 

support and interest shown by the staff at the STP were very important to us and we 

sincerely thank them. 

 
85

The Department of the Interior Mission

As the Nation's principal conservation agency, the Department of the Interior has responsibility for most of our 

nationally owned public lands and natural resources. This includes fostering sound use of our land and water 

resources; protecting our fish, wildlife, and biological diversity; preserving the environmental and cultural values of 

our national parks and historical places; and providing for the enjoyment of life through outdoor recreation. The 

Department assesses our energy and mineral resources and works to ensure that their development is in the best 

interests of all our people by encouraging stewardship and citizen participation in their care. The Department also 

has a major responsibility for American Indian reservation communities and for people who live in island territories 

under U.S. administration. 

The Minerals Management Service Mission 

As a bureau of the Department of the Interior, the Minerals Management Service's (MMS) primary responsibilities 

are to manage the mineral resources located on the Nation's Outer Continental Shelf (OCS), collect revenue from 

the Federal OCS and onshore Federal and Indian lands, and distribute those revenues. 

Moreover, in working to meet its responsibilities, the Offshore Minerals Management Program administers the 

OCS competitive leasing program and oversees the safe and environmentally sound exploration and production of 

our Nation's offshore natural gas, oil and other mineral resources. The MMS Royalty Management Program

meets its responsibilities by ensuring the efficient, timely and accurate collection and disbursement of revenue from 

mineral leasing and production due to Indian tribes and allottees, States and the U.S. Treasury. 

The MMS strives to fulfill its responsibilities through the general guiding principles of: (1) being responsive to the 

public's concerns and interests by maintaining a dialogue with all potentially affected parties and (2) carrying out its 

programs with an emphasis on working to enhance the quality of life for all Americans by lending MMS assistance 

and expertise to economic development and environmental protection. 
86