HomeMy WebLinkAboutStaff Report 6777
City of Palo Alto (ID # 6777)
City Council Staff Report
Report Type: Consent Calendar Meeting Date: 5/9/2016
City of Palo Alto Page 1
Summary Title: Approval of Contract with The United States Geological
Survey for San Francisco Bay Monitoring
Title: Approval of a Contract With the United States Geological Survey for
Five Years in the Amount of $60,023 per Year for a Total of $310,315 fo r San
Francisco Bay Monitoring Near the Regional Water Quality Control Plant's
Discharge
From: City Manager
Lead Department: Public Works
Recommendation
Staff recommends that Council approve and authorize the City Manager or his
designee to execute the attached sole source funding Agreement (Attachment A)
with United States Geological Survey (USGS) in the amount of $62,023 per year
for a term of five years for a total of $310,115 to monitor pollutants in clam tissue
and sediments and to monitor ecosystem diversity in the Palo Alto Baylands.
Background
The USGS has collected clam and sediment data adjacent to the Palo Alto
discharge point since 1974. The discharge point has been the source of
considerable data on diversity and clam reproductivity, as well. The work done by
the USGS consists of two parts. Part I provides for sampling and analysis of tissue
from clams and sediment found in the mud flats near the discharge point of the
Regional Water Quality Control Plant (RWQCP). Part II provides for monitoring of
the number and diversity of the benthic organisms (such as worms and clams that
live in the mud) and the reproductivity of the clams. The monitoring is required by
the San Francisco Bay Regional Water Quality Control Board (Regional Board),
which regulates the discharge of treated wastewater to the San Francisco Bay
from the RWQCP. The sampling will cover a five-year calendar period from 2017
to 2021 and continue the work approved by Council and completed during
City of Palo Alto Page 2
previous years (CMR:3514; CMR:164:10).
Discussion
The results to date show dramatic decreases in pollutant levels in the clams
compared to the early 1980s when pollutant discharges from RWQCP were much
greater. Part II of the program has shown the clams are better able to reproduce
and that certain other benthic organisms are on the increase, consistent with a
less contaminated environment. No other consultants or institutions have the
unique capability to analyze pollutant and ecosystem trends in the vicinity. The
work done by the USGS for Palo Alto to date has been exemplary and received
nationwide recognition. The USGS does not charge Palo Alto the full cost of the
sampling program, but only incremental costs associated with Palo Alto’s required
monitoring. The Regional Board and Palo Alto wish to take advantage of the
knowledge, experience, and efficiency in analyzing and interpreting data USGS
brings to this project. For these reasons, the USGS has been declared a sole
source provider of the required services.
Resource Impact
The total cost of the three-year agreement is $186,000. First year costs (in the
amount of $62,023) will be funded from the Wastewater Treatment Funds FY
2017 operating budget. Future years will be subject to Council approval of
Wastewater Treatment Fund budgets. These costs are shared with the partnering
cities which pick-up 64 percent.
Policy Implications
Approving this continuing monitoring program does not have any new policy
implications.
Environmental Review
The monitoring program does not constitute a project under the California
Environmental Quality Act (CEQA) and, therefore, an environmental assessment is
not required.
Attachments:
Attachment A: USGS - PaloAlto Collaboration Agreement (PDF)
Attachment B: USGS PA Proposal 2016 (DOCX)
March 2015 Agreement # 16HWCH00002
OPA File # 16-5087
1
Collaborative Agreement
Agreement between U.S. Geological Survey, a Bureau of the Department of the Interior, through the
offices of its National Research Program – Western Branch , located in Menlo Park, CA, hereinafter
called “USGS”; and the City of Palo Alto, located in Palo Alto, CA, hereinafter called “Collaborator.” USGS and Collaborator are sometimes herein referred to as a “Party” and collectively as the “Parties”.
Additional provisions that are specified in attachments to this Agreement are accepted to the extent
allowed by applicable Federal laws and regulations. If there are any conflicts between such attachments and this Agreement, the Parties understand that the provisions in Articles 1-14 shall take precedence.
Whereas, the USGS is authorized to perform collaborative work and prosecute projects in cooperation with other agencies, Federal, State or private, pursuant to 43 USC §36c and to receive payments in arrears
by 43 USC §50b.
Whereas, the USGS has a mission in basic and applied research of the nation’s water resources and has
need of data to support specific scientific objectives in understanding the dynamics of the San Francisco
Bay ecosystem relative to water and sediment quality;
Whereas, Collaborator has obligations to conduct a prescribed self-monitoring system of effluent
discharged to San Francisco Bay and has need of USGS expertise in inorganic biochemistry and estuarine
ecology;
Now therefore, the parties hereto agree as follows:
1. Statement of Work: See attached Statement of Work (SOW)(Attachment A), incorporated by referenceherein.
2.Principal Contacts: The Principal Investigator assigned to this project from the USGS is Dr. JanetThompson, 650-329-4364, jthompso@usgs.gov, 345 Middlefield Rd MS496, Menlo Park, CA 94025.
The Principal Contact for Collaborator is Karin North, 650-329-2104, Karin.north@cityofpaloalto.org,
2501 Embarcadero Way, Palo Alto, CA 94303. In the event that a PI is unable to continue in this project, the sponsoring agency will make every effort to substitute a replacement acceptable to the other Party.
3.Title to Equipment. There will be no joint property purchased as a result of the work outlined in theSOW. Each Party will provide its own equipment necessary to support its participation in the technical
evaluation.
4.Term. The collaborative effort provided by USGS and Collaborator will commence on the effective
date of this Agreement. The effective date of this agreement shall be the later date of (1) May 1, 2016 or (2) the date of the last signature by the Parties. The expiration date of this Agreement shall be April 30, 2021. This Agreement is subject to renewal only by mutual written agreement of the Parties.
5.Funding. Collaborator is providing funds to USGS in the amount of $310,115. The USGS requires anadvance of $0.00 to begin work on the project.
USGS shall issue an invoice to Collaborator for annual payments. Collaborator shall pay USGS in annual installments of $62,023 each on May 1, 2017, May 1, 2018, May 1, 2019, May 1, 2020, and May 1, 2021.
Attachment A
March 2015 Agreement # 16HWCH00002
OPA File # 16-5087
2
If work begins or continues prior to receiving a lump sum or installment advance payment, invoices not paid
within 60 days of receipt bear interest at the annual rate established by the U.S. Treasury.
The USGS will submit invoices on an annual basis to the administrative contact identified in Article 9.
Invoices not paid within 60 days of receipt bear interest at the annual rate established by the U.S.
Treasury, pursuant to 31 USC §3717.
Collaborator is providing in-kind services valued at $0.00.
USGS is providing in-kind services valued at $0.00.
6. Termination: This Agreement may be terminated by either Party on thirty (30) days written notice to the other Party. In the event of an early termination USGS shall be reimbursed for any completed work or
work in progress at the time of termination of the Agreement. 7. Publications/Reports: Each Party is free to publish the information and data developed by the project.
8. Intellectual Property: No intellectual property is expected to be developed under the research effort. A copy of the data and the reports provided for in the SOW will be delivered to Collaborator at the end of
the project.
9. Notices: Any notice required to be given or which shall be given under this Agreement shall be in
writing and delivered by first class mail to the parties as follows:
USGS: Collaborator:
Casey Tharp Karin North
345 Middlefield Rd MS466 2501 Embarcadero Way
Menlo Park, CA 94025 Palo Alto, CA 94303 ctharp@usgs.gov Karin.north@cityofpaloalto.org
650-329-4457 650-329-2104
Financial Contact Information for Collaborator: Karin North 2501 Embarcadero Way
Palo Alto, CA 94303 650-329-2104 Taxpayer ID: 94-6000389
www.cityofpaloalto.org
10. Independent Entity: For purposes of this Agreement and all services to be provided hereunder, each Party shall be, and shall be deemed to be, an independent party and not an agent or employee of the other party. Each Party shall have exclusive control over its employees in the performance of the work.
Neither Party may use the name of the other in advertising or other form of publicity without the written
permission of the other.
11. Governing Law/Disclaimer:
March 2015 Agreement # 16HWCH00002
OPA File # 16-5087
3
(a) The validity and interpretation of this Agreement are subject to interpretation under Federal Law.
Each party agrees to be responsible for the activities, including the negligence, of their employees. As a
Federal entity, USGS liability is limited by the Federal Tort Claims Act, codified at 28 USC 2671 et seq.
USGS warrants that it is self-insured for purposes of Worker’s Compensation.
(b) THE USGS AND COLLABORATOR MAKE NO EXPRESS OR IMPLIED WARRANTY AS TO THE
CONDITIONS OF THE RESEARCH, MERCHANTABILITY OR FITNESS FOR A PARTICULAR PURPOSE OF
THE RESEARCH, DATA OR RESULTING PRODUCT INCORPORATING DATA DEVELOPED AND
EXCHANGED UNDER THE STATEMENT OF WORK. THESE PROVISIONS SHALL SURVIVE THE
TERMINATION OF THE AGREEMENT.
12. Force Majeure. Neither Party shall be liable for any unforeseeable event beyond its control, not
caused by the fault or negligence of such Party, which causes such Party to be unable to perform its obligations under this Agreement, and which it is unable to overcome by the exercise of due diligence including, but not limited to, flood, drought, earthquake, storm, fire, pestilence, lightning, and other
natural catastrophes; epidemic, war, riot, civil disturbance, or disobedience; strikes, labor disputes, or failure, threat of failure, or sabotage; or any order or injunction made by a court or public agency. In the event of the occurrence of such a force majeure event, the Party unable to perform shall promptly notify
the other Party. It shall further use its best efforts to resume performance as quickly as possible and shall suspend performance only for such period of time as is necessary as a result of the force majeure event.
13. Entire Agreement: This Agreement contains all of the terms of the Parties and supercedes all prior agreements and understandings related thereto. This Agreement can be changed or amended only by a
written instrument signed by the Parties.
14. Disputes: The signatories to this Agreement shall expend their best efforts to amicably resolve any
dispute that may arise under this Agreement. Any dispute that the signatories are unable to resolve shall be submitted to the Director of the USGS or his/her designee and the City Manager of the Collaborator or his/her designee for resolution.
15. Miscellaneous Provisions: Pursuant to the Anti-Deficiency Act, codified at 31 U.S.C. §1341 (a)(1), nothing herein contained shall be construed as binding the USGS to expend in any one fiscal year any
sum in excess of its appropriations or funding in excess or what it has received for the collaborative work outlined in the SOW.
Non- Appropriation: This Agreement is subject to the fiscal provisions of the Charter of the City of Palo Alto and the Palo Alto
Municipal Code. This Agreement will terminate without any penalty (a) at the end of any fiscal year in
the event that funds are not appropriated for the following fiscal year, or (b) at any time within a fiscal year in the event that funds are only appropriated for a portion of the fiscal year and funds for this
Agreement are no longer available. This section shall take precedence in the event of a conflict with any
other covenant, term, condition, or provision of this Agreement.
16. Survivability. The following provisions shall survive the termination of this Agreement: 1, 3, 5-8, 10-16.
1
Attachment B
PROPOSAL TO THE CITY OF PALO ALTO:
NEAR FIELD RECEIVING WATER MONITORING
January 1, 2016 through December 31, 2020
U. S. GEOLOGICAL SURVEY
Dan Cain, Janet Thompson, Francis Parchaso, and Samuel Luoma (emeritus)
345 MIDDLEFIELD ROAD
MENLO PARK, CA 94025
2
Contents
Executive Summary of Past Findings ............................................................................................................. 3
Introduction .................................................................................................................................................. 6
Previous Studies in Near-Field Receiving Waters .......................................................................................... 7
Objectives .................................................................................................................................................... 10
Monitoring Approach .................................................................................................................................. 11
Sampling Design ...................................................................................................................................... 12
Sampling Location............................................................................................................................... 12
Sampling Frequency ........................................................................................................................... 13
Constituents to be Determined .......................................................................................................... 13
Methods .................................................................................................................................................. 14
Sampling ............................................................................................................................................. 14
Sample Preparation ............................................................................................................................ 14
Analytical Methods ............................................................................................................................. 16
Data Analysis ...................................................................................................................................... 17
Products ...................................................................................................................................................... 17
Budget ......................................................................................................................................................... 18
3
Executive Summary of Past Findings
U.S. Geological Survey (USGS) scientists have assessed trace metal concentrations in sediments and
sediment-dwelling species at an intertidal site in the vicinity of the discharge point of the Palo Alto
Regional Water Quality Control Plant (RWQCP) since 1977. They have also characterized the area’s
benthic community structure since 1974. Ancillary biotic and abiotic factors that could affect metal
concentrations and benthic community structure—exotic species invasions, pelagic food availability, and
weather anomalies—have also been measured during this time. Collectively, this dataset describes a
long-term, detailed history of metal concentrations and benthic community dynamics at this site. It
provides a detailed chronology of ecological recovery following reductions in metal loadings from
RWQCP, and continues to support the management of metal contaminants in San Francisco Bay.
Initially, these studies found exceptionally high concentrations of copper (Cu) and silver (Ag) in mud-
dwelling animals in this area, with strong seasonal variability. Additional studies identified the RWQCP as
a point source for Cu and Ag and established the clam Macoma petalum as a biological indicator of
metal exposure. The annual mean concentrations of Cu and Ag in M. petalum were 287 mg/kg and 105
mg/kg, respectively, in 1980. These levels exceeded tissue concentrations reported in the literature for
this species and were much greater than seen elsewhere in San Francisco Bay. Elevated metal
concentrations coincided with reduced reproductive activity in M. petalum. Related studies supported
the hypothesis that elevated Ag concentrations in M. petalum inhibited the development of
reproductive tissue. The benthic community also showed signs of environmental stress during this time,
suggesting that metal exposures were affecting the species composition of the community.
Opportunistic organisms (capable of fast invasion and propagation in disturbed environments)
dominated the community. These organisms possess traits that could reduce contact with highly
contaminated sediments (e.g., live at the sediment-water interface, in tubes, or as shelled animals;
brood their young; and fed on waterborne particles rather than on sediment).
Concentrations of Cu and Ag in both sediments and clams declined significantly during the 1980s as the
PARWQCP implemented more advanced waste-water treatment and source control programs. The
downward trends in Cu in sediments and in the tissues of M. petalum correlated with reduced Cu
discharge from the RWQCP. Coincident with the decline in Cu and Ag in the sediment and clams, the
4
reproductive activity of the clam greatly increased. The composition of the benthic community also
shifted during this period. Opportunistic species became less dominant, and less opportunistic species
became more persistent. Other environmental factors that vary seasonally and annually (for example,
sediment composition, grain-size distribution, organic content, and ambient water salinity) were not
associated with the observed temporal trends in metal concentrations, inferred metal effects on
species, and benthic community changes. The only unidirectional change in an environmental factor
during this period (1980–1990) was the decline in metal concentrations in discharge from the waste
treatment plant.
Following the significant reductions in the 1980s, concentrations of Cu and Ag in sediments and clams
have remained relatively low and stable. Concentrations have fluctuated modestly and without a
sustained temporal trend. However, Ag in sediments remains greater than what may be considered the
regional background (0.09 mg/kg). This persistent, low level of contamination likely derives from Ag
introduced to the site before the 1990s. The concentrations of Cu and Ag in M. petalum have fluctuated
as much as four-fold. Concentration minima for Cu observed during this period (1991, 2000–2005, and
2008–2012) were comparable to what can be considered baseline concentrations for this species in San
Francisco Bay (20–30 mg/kg). Thus, metal concentrations in sediments and tissue of M. petalum are
more likely a combination of inputs from the PARWQP and other regional sources, cycling of
contaminants stored within sediments, and regionally-scaled physical and biogeochemical processes
controlling the distribution and bioavailability of metals.
As concentrations of Ag and Cu in M. petalum declined, reproductive activity increased both in terms of
the percentage of individuals that were in a reproductively active stage and the frequency of
reproductive activity during the year. Overall, the reproductive status of the population has improved
and stabilized over the 20 years of reduced exposure to Ag and Cu at the site.
Over the same period, the composition of the infaunal community shifted from a dominance of surface-
dwelling, brooding species to species with various life-history characteristics. In particular, species that
lay their eggs in the mud and feed by burrowing through and consuming the mud, which were rare in
the community in the 1970s and 1980s, have increased in abundance. This pattern continued through
2007, with the less opportunistic species becoming more dominant in abundance. A disturbance
occurred on the mudflat in early 2008 (possible causes include sediment accretion or freshwater
5
inundation) that resulted in the loss of the benthic animals, except for those deep-dwelling animals like
M. petalum. Animals returned to the mudflat within 2 months of the event, however, which indicated
that the disturbance was not due to a persistent toxin or to anoxia. Benthic community data in 2009
showed that the animals that returned to the mudflat were those that can respond successfully to a
physical, nontoxic disturbance. The most recent community surveys showed a mix of animals that
consume the sediment, filter feed, brood their young, and have pelagic larvae that must survive life on
the sediment at a young age. The 2008 defaunation event allowed for an examination of the response of
the community to a natural disturbance and a comparison of this recovery to the long-term recovery
observed in the 1970s, when the decline in sediment pollutants was the dominating factor. Today, the
community at this site is very similar to the benthic community observed by Thompson and Parchaso
(2012) throughout South San Francisco Bay: although small filter feeding species are numerically
dominant, there is a significant proportion of the community that feeds on surface and subsurface
sediment particles, a feature of community structure that is not present where sediments have high
concentrations of toxicants.
When this study started in the late 1970s, the site was already heavily contaminated with metals.
Although the authors assume that the biological conditions reflected the consequences of elevated
metal exposures, there is a scarcity of preexisting data to evaluate impacts due to elevated metals.
However, the long-term record contained in this study provides a unique opportunity to document
biological response when the stress of metal exposure is relaxed. The data make a compelling case that
the mitigation of Ag and Cu in waste-water effluent during the 1980s allowed for biological recovery and
the establishment of a more diverse and stable infaunal community.
Programs to control and reduce loadings of priority pollutants, including, Cu, Ag, Ni, and Hg to South Bay
and monitoring of those pollutants continue. By monitoring metal concentrations and community
dynamics, this study supports the self-monitoring and reporting programs of RWQCP, and compliments
the Regional Monitoring Program (RMP). In addition to providing an historical perspective and current
status of environmental conditions in the extreme South Bay, data from this study are constructing a
contemporary baseline to identify future perturbations to the benthic community. Human impacts on
the Bay ecosystem will continue. Events that have the potential of altering the observed contamination
in the system include (1) the ongoing salt pond restoration which could mobilize old and new sediments
and change the hydrodynamics of South Bay, and (2) emerging contaminants, such as the rapidly
6
expanding commercialization of consumer products utilizing metal-based nanoparticles. An important
implication of our recent findings is that effects on metal contamination from these changes have not
proven to be sufficient to be detectable in the present South Bay environment.
Other changing environmental conditions will also shape ecological patterns in South Bay. For example,
recent changes in the seasonal pattern of phytoplankton growth and accumulation (blooms) in South
Bay are likely to affect and be affected by the benthic community. We have seen a significant increase
in the background levels of phytoplankton biomass in the south bay since 1999. We have also observed a
fall phytoplankton bloom in addition to the spring bloom during many years since 1999. There are a
number of possible factors contributing to these changes in phytoplankton dynamics. Two strong
possibilities include (1) a change in light availability due to lower suspended sediment concentrations, or
(2) smaller populations of filter feeding bivalves that normally heavily graze the phytoplankton during all
periods except early spring. It is also likely that these changes would not be occurring if metal
contamination was sufficient to inhibit phytoplankton growth.
Introduction
In the 1992, the California Regional Water Quality Control Board (RWCB) directed the Executive Office to
implement a regional monitoring program for San Francisco Bay, currently known as the San Francisco
Bay Regional Monitoring Program for Trace Substances (RMP). Furthermore, the RWCB directed
discharge permit holders to implement a self-monitoring program comprising the collection of chemical
data for water, sediment, and biota from receiving waters in support of the RMP. The RWQCP conducts
self-monitoring of receiving water as a condition of its NPDES permit. Since 1994, the City of Palo Alto
has also supported special U. S. Geological Survey (USGS) studies of metals and benthic community
structure at a site near the RWQCP discharge point. USGS scientists have studied this site since the mid-
1970’s using methods compatible with the RMP. This dataset is the basis for a long-term temporal
perspective of ecological conditions in the extreme South Bay. The program has had demonstrated
successes with respect to management of pollutant discharge to the Bay: documenting a progressive
reduction of metal contamination near the discharge of the RWQCP; identifying regional and local factors
contributing to more complicated temporal patterns in metal concentrations in biota and sediments;
and continuing monitoring of priority pollutants, including copper, nickel, and mercury. By
7
currently studying metals and benthic community structure, a strong linkage between metal exposures
and biological responses was established.
Looking forward, our understanding of water quality and the ecosystem needs to consider on-going and
planned activities that could influence metals and biological communities in South Bay. For example, the
South Bay Salt Pond Restoration Project completed the physical restructuring of the ponds in 2014.
Remobilized sediment and water from these ponds has been transported throughout South Bay, and
likely to the USGS field site. The potential of these newly created habitats to be sources of metals, such
as Hg, is currently being studied. In addition, recent increases in phytoplankton biomass in South Bay
since 1999 (Cloern and others, 2007) and the apparent causes of the increase (influx of predators on the
benthos and decreased turbidity) are likely to be reflected in the benthic community structure if the
higher phytoplankton biomass persists. Analysis of community structure will identify long-term shifts in
species composition as well as episodic disturbances. Monitoring of metals will contribute to a strength-
of-evidence approach to assess potential causes for observed changes in community structure.
The present proposal is for the five year period starting on January 1, 2016 and ending on December 31,
2020. The proposal describes a continuation of the near-field (inshore) monitoring program at the USGS
site that builds upon a rare long-term ecological record spanning four decades. We propose to
accompany assessments of trends in metal exposure with determinations of biological processes that
integrate and respond to environmental perturbations on different temporal scales. Specifically,
reproduction in the indicator clam, M. petalum, and benthic community structure will be assessed.
Monitoring metal concentrations and biological endpoints will provide a robust evaluation of site-
specific ecological condition that is compatible with the RWCB’s goals.
Previous Studies in Near-Field Receiving Waters
USGS scientists began collecting biological, physical, and chemical data from an intertidal mudflat near
the discharge point of the RWQP in the mid-1970’s. These data showed exceptionally high
concentrations of copper (Cu) and silver (Ag) in surficial sediments and in the clam M. petalum at this
site compared to other locations in the Bay and worldwide (Thomson and others, 1984; Luoma and
others, 1985; Cain and Luoma 1990). USGS studies also indicated that the reproductive cycle of M.
petalum was abnormal, and the assemblage of benthic species was indicative of environmental stress.
8
Additional studies, showed metals were present in enriched concentrations throughout the food web,
including birds from the area.
Concentrations of Cu and Ag declined in both sediments and M. petalum after 1981 as the RWQCP
implemented advanced treatment of influent and source control programs. The downward trends in Cu
in sediments and in the clam correlated with reduced Cu discharges from the RWQCP. The intertidal
mudflat environment of the site is quite complex and variable from year-to-year. Sediment composition
(for example mean particle size and organic content), salinity, and other factors varied seasonally and
from one year to another. However, over a sustained period of study none of these factors displayed
temporal trends that corresponded to the changes in metal concentrations, metal effects, or benthic
community changes. The only unidirectional change in an environmental factor during this period was
the decline in metal inputs from the waste treatment plant during the 1980s. Since 1991, metal
concentrations in M. petalum more or less stabilized around 40 µg/g Cu and 4 µg/g Ag. Annual variations
in tissue metal concentrations of relatively small magnitude occur, but there have been no sustained
trends, and the temporal patterns no longer correlate with Cu and Ag discharged from the plant.
Although effluent from the plant contributes to the metal loading of South Bay, the data suggest it does
not have the predominant influence on metal concentrations at the site that it did historically. Seasonal
fluctuations and annual variation in metal concentrations now are more likely related to a combination
of factors such as local inputs, diffuse and periodic inputs (e.g., storm related run-off),
remobilization/recycling of legacy contamination of Bay sediments, and local physicochemical conditions
affecting metal bioavailability.
Since 1974, USGS scientists have also monitored and studied the benthic community and reproductive
activity of M. petalum at the site. Findings during the first 10 years of this study were published in
Nichols and Thompson (1985a; 1985b). We found that this community was composed of non-
indigenous, opportunistic species that dominated the community due to their ability to survive the
many physical disturbances on the mudflat. The disturbances discussed included sediment erosion and
deposition, and exposure at extreme low tides. The possible effects of metal exposure as a disturbance
factor were not considered in these analyses as the decline in metal concentrations in M. petalum and
sediment had just begun.
A synthesis of results from the metal study (see Hornberger and others, 1999; 2000) suggested that
9
sediments and local populations of clams at this location are sensitive indicators of metal loadings to
nearby receiving waters. These studies illustrated reduced metal concentrations in sediments and in
biota (M. petalum) within a year of significant reductions in metal loading from the RWQCP discharge.
Other analyses (e.g., Thompson and others, 2002; Shouse 2002; Shouse and others, 2003; Moon and
others, 2005, Cain and others, 2006) indicated that higher-level biological responses to metal loading
take longer. Whereas a response at the organism level (i.e., reproductive activity) was observed within a
year or two, a consistent response at the community level, indicated by a progressive change in the
number or type of species that colonized the site following the recession in metals exposure, took several
years to develop. Due to the natural intra-annual variability of benthic community dynamics it is likely
to take a minimum of 5-10 years for a change in the benthic community to be stable.
Analyses of the benthic community data have revealed the following trends:
1. The community has shifted from being dominated by a few opportunistic species to a
community where there are more equally dominant, equally persistent species;
2. The community, which was previously dominated by surface dwelling, brooding species in now
composed of species with varying life history characteristics;
3. Species that lay their eggs in the mud, previously rarely present in the community, have
increased in abundance;
4. M. petalum reproductive activity has increased concurrent with the decline in tissue metal
concentrations, resulting in a population with predictable semi-annual reproductive periods.
These studies demonstrated how coordinated monitoring of metals exposure and biological response
can strengthen interpretations of causality. The strong temporal associations among metal loading,
environmental levels of metal contamination, and biological responses support an interpretation of
biological recovery following a recession of metal exposures resulting from reductions in metal loadings
to South Bay by municipal and industrial dischargers in general, and RWQCP in particular. Temporally
intensive sampling (multiple months per year) facilitated identification of long-term trends from annual
and intra-annual variation driven by climate patterns and growth and reproductive cycles in benthic
invertebrates. The data from a receiving water-monitoring program of this type is useful for the Regional
Board, and it can provide valuable feedback to local dischargers. For example, these data help to inform
10
staff at the RWQP on plant operations, and the success of source control and pretreatment programs.
Objectives
The purpose of this monitoring program is to characterize temporal trends in trace element
concentrations, the reproductive activity of the bioindicator, M. petalum, and the benthic community
structure at an inshore (intertidal) site near the discharge of the RWQCP (i.e., the USGS site), as
designated in the RWQCP self-monitoring program. Specifically, trace elements and associated
parameters will be determined in surficial, fine-grained sediments and in the clam M. petalum, the
reproductive state of M. petalum will be evaluated, and the structural and functional features of the
benthic community will be analyzed. Biological attributes will be characterized with simple, established
metrics. Reproductive activity will be reported as total percentage of animals reproductively active for
each year (we know from previous work that this percentage is lowest during periods with the highest
pollutant concentrations (Hornberger and others, 1999, 2000)) and as a reproductive index. Community
composition will be described in terms of number of species, number of individuals of dominant species
and rank analysis curves (i.e. benthic communities in more polluted environments are expected to have
fewer species and higher numbers of individuals for the dominant species than benthic communities in
non-polluted environments). All monitoring will be conducted in a manner that will provide high-
quality data that are compatible with existing data, and with data provided by programs such as the
Regional Monitoring Program.
Specific objectives include:
1. Collect data to assess seasonal patterns and inter-annual trends in trace element
concentrations in sediments and M. petalum at the USGS site;
2. Collect ancillary chemical and physical data to monitor seasonal and inter-annual patterns in
environmental conditions at the site;
3. Collect data to assess seasonal and annual trends in reproductive activity of the clam M.
petalum at the site;
4. Collect data to assess seasonal and annual trends in benthic community structure at the USGS
site, concurrent with metals data;
11
5. Present the data within the context of the historical dataset from the site so as to characterize
long-term trends and current conditions;
6. Provide data complementary to and supportive of other South Bay programs such as the RMP.
Despite the complexities of monitoring natural systems, the monitoring approach described below has
been effective in the past in relating changes in near field contamination in San Francisco Bay to changes
in metal discharges to the Bay, and in relating changes in near field contamination to changes in benthic
community structure (Kennish, 1998) and reproductive activity of M. petalum (Hornberger and others,
2000). Existing historical data will provide a context within which cause and effect can be assessed for
change in the future. If continued, this study will provide data on metal concentrations in the local
receiving water that can be evaluated within the context of similar data collected by Regional
Monitoring Program, feed-back on new or on-going initiatives to control and mitigate inputs of metals
from sources within the service area, and new treatment technologies to reduce effluent loadings.
Continuation of this study will build on a unique data set where ecological data and contaminant data
are concurrently collected and analyzed within the context of changing influent treatment practices.
Monitoring Approach
The proposed approach will monitor trace element concentrations in fine-grained (< 100 µm) sediments
and the resident population of the deposit-feeding clam M. petalum. Sediment particles bind most trace
element pollutants strongly, efficiently removing them from the water column. Numerous prior studies
have shown that analysis of concentrations of these pollutants in sediments provide a time-
integrated indicator of trace element input to the water column. Animals such as M. petalum live in
contact with sediments and feed upon organic material associated with sediment particles. Uptake of
trace elements from ingested sediments results in their accumulation in the tissues of M. petalum.
These animals are important prey for larger species that live in the Bay, including migrating waterfowl.
Thus, analysis of the metals in the soft tissues of the clam provides a measure of the clam’s exposure to
bioavailable pollutants and an estimate metal transfer to predators.
Analysis of the trace element concentration in the tissues of a bioindicator, such as M. petalum,
indicates whether a pollutant is bioavailable and bioaccumulated. Although elevated pollutant
concentrations in an organism suggest an increased probability of toxicological risk, it does not confirm
12
toxicity. Chronic metal toxicity in an invertebrate can manifest in physiological impairment, including
reproductive impairment (Hook and Fisher, 2001a; 2001b), feeding inhibition (Cain and others, 2016),
and retarded growth (Irving and others, 2003). Annual growth and reproductive cycles in M. petalum
can be followed with the condition index (CI), which is an indicator of the physiological condition of the
animal and, specifically, is the total soft-tissue weight of a clam standardized to shell length (Cain and
others, 1990). Earlier studies of M. petalum from the USGS site showed that reproductive activity
increased as Cu and Ag concentrations in the clam’s soft tissues declined (Hornberger and others, 2000).
Therefore, the CI and reproductive activity of M. petalum appears to be a good indicators of
physiological stress related to elevated exposure to some metals, at least.
The benthic community data will be analyzed in a manner similar to that used in published benthic
studies near sewage treatment outfalls (see Kennish 1998). The proposed approach will examine
species dominance patterns and community composition changes in combination with environmental
variables. Other studies have shown that more opportunistic species are likely to persist in highly
disturbed environments (as was shown by Nichols and Thompson (1985a) at this location in 1974
through 1983), and that the abundance and types of dominant species can change with changes in
metal concentrations (Shouse and others, 2003). We will also examine changes in the benthic
community concurrent with changes in the concentrations of specific metals. For example it has been
shown that some crustacean and polychaete species are particularly sensitive to elevated copper
(Morrisey and others, 1996; Rygg 1985) and that most taxonomic groups have species that are sensitive
to elevated silver (Luoma and others, 1995).
Sampling Design
Sampling Location
Samples for sediment and clam tissue metal concentrations will be collected from an intertidal mudflat
site located at Sand Point (N 37º 27.638, W 122º 05.969) (Figure 1). Benthic community samples will be
collected nearby (Figure 1): station FN45 is 12 m from the edge of the marsh and 110 cm above MLLW.
These locations are on a mudflat on the shore of the bay (not a slough) approximately 1 kilometer
southeast of the Palo Alto discharge point. It was chosen because it is influenced by the discharge of
RWQCP, but it is not immediately adjacent to that discharge. Thus, it reflects a response of receiving
13
waters to the effluent, beyond just a measure of the effluent itself. Earlier studies have shown that
dyes, natural organic materials in San Francisquito Creek and effluent from the RWQCP all move
predominantly south toward Sand Point and thereby influence the mudflats in the vicinity. Earlier work
showed that San Francisquito Creek and the historical Yacht Harbor were minor sources of most trace
elements compared to the RWQCP. Earlier studies also showed that intensive monitoring at one site
was more effective in determining trends in trace element contamination than was less frequent
sampling at a larger number of sites in the vicinity of the discharge.
Sampling Frequency
The basic metals monitoring program supported by the City of Palo Alto will have a sampling frequency
of three times per year. Statistical techniques such as power analyses indicate that three samples per
year will provide 20 percent sensitivity in detecting trends. The USGS monitoring experience at the site
indicates that seasonal cycles and episodic events influence annual variation in metal concentrations in
sediments and tissues; three samples per year will be insufficient to track and characterize seasonality in
metal contamination. Consequently, important episodic events may be missed, associations between
metals and biological metrics, such as community structure, are weakened, and long-term trends in both
metal exposure and community composition are more difficult to define. Thus, samples will be collected
more frequently as stipulated below.
To support interpretations of cause and effect in a temporally variable environment, metal and benthic
invertebrate sampling should be coincident and thus sampling will coincide with the three sampling
events for metals. In addition, previous analyses of benthic invertebrate data (1974 through 1983)
indicated that benthic samples need to be collected at a time step of about every other month in order
to distinguish seasonal differences from inter-annual differences if the differences are small (Nichols and
Thompson 1985a; 1985b). In dynamic systems such as San Francisco Bay, distinguishing between the
effects of natural seasonal changes and anthropogenic environmental stressors is more reliable with
more frequent samples. Thus, the USGS will sample metals in the sediment and clam tissue and will
sample the benthic community an additional two to six times per year.
Constituents to be Determined
The chemical constituents to be analyzed in sediments and in the tissues of M. petalum as well as
14
ancillary chemistry and physical properties are listed in Table 1. The constituent list is consistent with
the chemical and physical constituents analyzed by the RMP. The methods employed are designed to
minimize below detection limit determinations. The variables chosen for determination are those
required by the Regional Board.
Benthic samples will be processed to produce species lists, species counts, and species functional group.
Each clam selected for reproductive analysis will be characterized by size (length in mm), sex,
developmental stage, and condition of gonads.
Methods
Sampling
Sediments and M. petalum will be collected at low tide from the exposed mudflat. Sediment samples will
be scraped from the visibly oxidized (brownish) surface layer (top 1–2 cm) of mud. This surface layer
represents recently deposited sediment and detritus, or sediment affected by recent chemical reactions
with the water column. The sediment also supports microflora and fauna, a nutritional source ingested
by M. petalum. Enough sediment will be obtained to conduct all proposed analyses (Table 1) and to
archive approximately 10 grams for any unforeseen future needs. Clams will be collected by hand from
the same area. Typically, 60–120 individuals will be collected, representing a range of sizes (shell length).
As they are collected, the clams will be placed into screw-cap polypropylene container (previously acid-
washed) containing site water. These containers will be used to transport the clams to the laboratory.
Three replicate samples will be collected using 8.5 cm diameter x 20 cm deep cores for the benthic
community monitoring study. A minimum of 10 individual M. petalum of varying sizes (minimum of
5mm) will be collected for the analysis of reproductive activity.
Sample Preparation
Sediments will be sieved through 100 μm mesh in ultra-clean (18 Mohm-cm) deionized water
immediately upon return to the laboratory. Both the fraction of sediment passing through the sieve and
the fraction retained on the sieve will be dried and weighed. Particle size distribution will be defined as
the proportion of the total sediment mass divided between these two fractions. This also provides an
estimate of the particle size characteristics of the bulk sediment for those who might want to make
15
comparisons with bulk analyses.
Replicate aliquots of the fraction of sediment that passes through the 100 μm sieve will be digested by
reflux with concentrated nitric acid. This method provides a “near-total” extraction of metals from the
sediment and is comparable to the recommended procedures of the U.S. Environmental Protection
Agency (USEPA) for leachable metals and to the procedures employed in the Regional Monitoring
Program. Another set of replicate subsamples from the silt/clay fraction will be directly extracted with
dilute (0.6 N) hydrochloric acid (HCl) for 2 hours at room temperature. This method extracts metals
bound to sediment surfaces and is operationally designed to obtain the leachable, anthropogenic
contribution to the sediment concentration (Luoma and Bryan 1982).
Total organic carbon (TOC) concentrations were determined using a continuous flow isotope ratio mass
spectrophotometer (IRMS) (table 1). Before the analysis, sediment samples were acidified with 12 N HCl
vapor to remove inorganic carbon (Harris and others, 2001).
Clams will be returned to the laboratory live, washed free of local sediment and placed in clean ocean
water diluted with distilled water to the salinity on the mudflat at the time of collection (determined
from the water in the mantle cavity of representative individual clams). Clams will be moved to a
constant temperature room (12° C) and starved for 48 hours to allow for the egestion of sediment and
undigested material from their digestive tracts.
Following depuration, the length of each clam will be determined then the shell and soft tissue will be
separated. Soft tissues will be composited into 6-12 composite samples, each containing animals of
similar shell length, digested by nitric acid reflux, and analyzed for most metals by inductively coupled
plasma optical emission spectrophotometry (ICPOES). Samples for mercury and selenium analysis will
be composited as above into 3-4 composite samples. These samples will be stored at -80° C, and later
will be homogenized, refrozen, freeze dried, and subsampled for analysis (see below). The data from
these animals are not normally distributed and may be affected by animal size. Correlations will be
calculated between animal size and metal concentration, and established procedures will be employed
to calculate metal content of a standard sized clam for each collection to facilitate comparisons of metal
exposure over time. Previous studies show that such data reduction procedures are necessary to
account for biological factors (size and growth) that affect metal concentrations, thus allowing a clearer
linkage between RWQCP discharges and responses of the clams.
16
Benthic samples will be washed on a 0.5mm screen, preserved in 10% formalin for two weeks and then
transferred to 70% ethyl alcohol with Rose Bengal stain. Clams collected for reproductive analysis will
be immediately preserved in 10% formalin at the time of collection. In the laboratory, the visceral mass
of each clam will be removed, stored in 70% ethyl alcohol, and then prepared using standard histological
techniques: tissues will be dehydrated in a graded series of alcohol, cleared in toluene (twice for one
hour each), and infiltrated in a saturated solution of toluene and Paraplast for one hour and two changes
of melted Tissuemat for one hour each. Samples will then be embedded in Paraplast in a
vacuum chamber and then thin sectioned (10 micrometer) using a microtome. Sections will be stained
with Harris’ hematoxylin and eosin.
Analytical Methods
Digested tissue and sediment samples will be evaporated to dryness and reconstituted in 0.6N
hydrochloric acid. Most elements will be analyzed by (ICP-OES) (Table 1). Tissue and sediment samples
will be subsampled and analyzed for total mercury by acid-digestion, BrCl oxidation, purge and trap, and
cold vapor atomic fluorescence spectrometry according to the EPA Method1631, Revision E (2002), and
for selenium by acid digestion, hydrogen peroxide oxidation, hydride generation inductively coupled
plasma mass spectrometry (HG-ICP-MS) according to a method modified from Liber (2011) and Elrick &
Horowitz (1985).
Total organic carbon (TOC) concentrations were determined using a continuous flow isotope ratio mass
spectrophotometer (IRMS) (table 1). Before the analysis, sediment samples were acidified with 12 N HCl
vapor to remove inorganic carbon (Harris and others, 2001).
To minimize metal contamination of samples, all glassware and plastic used for sample collection,
preparation, and storage will be cleaned by sequentially washing with a detergent, deionized water
rinse, followed by a 10-percent hydrochloric-acid wash and double-deionized water (18 mega-ohm-cm
(MΩ-cm) resistivity) rinse. Materials will be dried in a dust-free positive-pressure environment, sealed,
and stored in a cabinet. Quality control will be maintained by frequent analysis of blanks, analysis of
National Institute of Standards and Technology standard reference materials (e.g., NIST 2709a, San
Joaquin soils, and NIST 2976, mussel tissue) with each analytical run, and internal comparisons with
prepared quality control standards. Method detection limits (MDL) and reporting levels (MRL) will be
determined using the procedures outlined by Glaser and others (1981), Childress and others (1999), and
17
U.S. Environmental Protection Agency (2004).
Benthic samples will be sorted and individuals identified to the lowest taxonomic level possible (some
groups are still not well defined in the bay, such as the oligochaetes), and individuals for each species
will be enumerated.
The stained thin sections of clam reproductive tissue will be examined with a light microscope. Each
individual will be characterized by size (length in mm), sex, developmental stage, and condition of
gonads, thus allowing each specimen to be placed in one of five qualitative classes of gonadal
development (Parchaso 1993).
Data Analysis
The period of sample collection is the calendar year. Annual data will be compiled, summarized, and
appended to the long-term dataset. Data for sediment chemistry and metal concentrations in the
bioindicator, M. petalum, will be assessed within the context of the long-term record as well as data
collected since 1994. Changes in elemental constituents and associations among those constituents and
with other environmental properties will be analyzed by parametric and non-parametric statistical
models, such as correlation and ANOVA.
The seasonal benthic community data will be examined using multivariate techniques (Shouse 2002).
Multivariate analyses will be used to identify connections between the environmental variables
(including body burdens of trace elements in bivalves and copper and silver sediment concentrations)
and benthic community structure. Data for individual species will also be examined to determine if
there are any population changes as a result of metal concentration changes. The time series for
individual species will be examined using annual and seasonal trends, and will be examined in
conjunction with time series of trace metal concentration. The reproductive stage data will be similarly
analyzed as a time series in conjunction with trace metal concentrations and benthic community data.
Products
Data will be summarized and reported to the City of Palo Alto at the completion of each annual sampling
period (i.e., calendar year). Annual reports will be consistent with the RMP reporting format.
Appendices will include basic analytical data and computations, quality assurance data, species lists,
18
species counts, species analysis by functional group, and basic analytical and computational data for the
benthic community and reproductive data. To meet the objectives of the study, the report will include
interpretive figures, tables and narrative descriptions of the most recent data in relation to the long-
term time series.
Budget
The budget for the proposed project is outlined in Table 2. This budget includes charges only for the
basic monitoring program of 3 sediment and clam tissue collections per year and for 4 benthic
community collections per year. The USGS will complement the study with additional collections in each
year which is reflected in the sampling frequency (Table 1). This proposal describes work that will begin
January 2016 and continue for five years, through December 2020. Renewal each January will be at the
discretion of the City of Palo Alto.
19
Cited Literature
California Regional Water Quality Control Board, San Francisco Bay Basin (Region 2) Water Quality
Control Plan (Basin Plan). http://www.waterboards.ca.gov/sanfranciscobay/basin_planning.shtml
Cain, D. J., and Luoma, S. N., 1990, Influence of seasonal growth, age and environmental exposure on Cu
and Ag in a bivalve indicator, Macoma balthica, in San Francisco Bay: Marine Ecology Progress Series, v.
60, p. 45-55.
Cain, D.J., F. Parchaso, J.K. Thompson, S.N. Luoma, A. H. Lorenzi, E. Moon, M.K. Shouse, M.I. Hornberger,
J.L. Dyke, and R. Cervantes, 2005, Near field receiving water monitoring of trace metals and a
benthic community near the Palo Alto Water Quality Control Plant in South San Francisco Bay,
California: 2005: U.S. Geological Survey Open File Report 2006-1152, 120 pp.
Cloern, J.E., Jassby, A.D., Thompson, J.K, Hieb, K. 2007. A cold phase of the east Pacific triggers new
phytoplankton blooms in San Francisco Bay: Proceedings National Academy of Science, v. 104, no.
47, p. 18561-18565.
Childress, C.J.O., Foreman, W.T., Connor, B.F., and Maloney, T.J., 1999, New reporting procedures based
on long-term method detection levels and some considerations for interpretations of water-quality
data: U.S. Geological Survey Open-File Report 99–193, 19 p.
Glaser, J.A., Foerst, D.L., Mckee, G.D., Quave, S.A., and Budde, W.L., 1981, Trace analyses for
wastewaters: Environmental Science and Technology, v. 15, no. 12, p. 1426–1435.
Hook, S.E. and Fisher, N.S., 2001a, Sublethal effects of silver in zooplankton: importance of exposure
pathways and implications for toxicity testing: Environmental Toxicology and Chemistry, v20: 568-
574.
Hook, S.E. and Fisher, N.S.,2001b,. Reproductive toxicity of metals in calando copepods: Marine Biology,
v.138:1131-1140.
Hornberger, M., S. Luoma, D. Cain, F. Parchaso, C. Brown, R. Bouse, C. Wellise, and J. Thompson, 1999,
Bioaccumulation of metals by the bivalve Macoma balthica at a site in South San Francisco Bay
between 1977 and 1997: Long-term trends and associated biological effects with changing pollutant
loadings: U.S. Geological Survey Open File Report 99-55, 42p.
20
Hornberger, M., Luoma, S. Cain, DParchaso, .F. Brown, C. Bouse, R. Wellise, C. and Thompson, J. 2000,
Linkage of bioaccumulation and biological effects to changes in pollutant loads in South San Francisco
Bay: Environmental Science and Technology, v.34:2401-2409.
Irving, E.C., Baird, D. J., and Culp, J.M., 2003, Ecotoxicological responses to the mayfly Baetis tricaudatus
to dietary and waterborne cadmium: implications for toxicity testing: Environmental Toxicology and
Chemistry, v.22: 1058-1064.
Kennish, J.K., 1998, Pollution impacts on marine biotic communities: CRC Press, New York. 310 pp.
Liber, K, 2011, Cold Digestion of Invertebrates for the Selenium Project. Method developed C.W. and
E.F. 2007. Revised Mar 2011 MK: Water Quality Laboratory, Toxicology Center, University of
Saskatchewan
Luoma, S.N. and Bryan, G.W., 1982, A statistical study of environmental factors controlling
concentrations of heavy metals in the burrowing bivalve Scrobicularia plana and the polychaete Neris
diversicolor: Estuararine Coastal and Shelf Science, v.15: 95-108.
Luoma, S.N., Cain, D.J., and Johansson, C., 1985, Temporal fluctuations of silver, copper and zinc in the
bivalve Macoma balthica at five stations in South San Francisco Bay: Hydrobiologia, v. 129, p. 109–
120.
Luoma, S.N., Y.B. Ho, and G. W. Bryan, 1995, Fate, bioavailability and toxicity of silver in estuarine
environments: Marine Pollution Bulletin, v.31:44-54
Moon, E., Shouse, M.K., Parchaso, F., Thompson, J.K., Luoma, S.N., Cain, D. J., and Hornberger, M. I. ,
2004, Near field receiving water monitoring of trace metals and a benthic community near the Palo
Alto Water Quality Control Plant in South San Francisco Bay, California: 2004: U.S. Geological Survey
Open File Report 2005-1279, 115 pp.
Morrisey, D.J., A.J. Underwood, and L. Howitt, 1996, Effects of copper on the faunas of marine soft-
sediments: an experimental field study: Marine Biology v.125:199-213
Nichols, F.N, and J.K. Thompson, 1985a, Persistence of an introduced mudflat community in South San
Francisco Bay, California. Marine Ecology Progress Series, v.24:83-97.
Nichols, F.N, and J.K. Thompson, 1985b, Time scales of change in the San Francisco Bay benthos:
Hydrobiologia, v 129:121-138.
21
Rygg, B., 1985, Effect of sediment copper on benthic fauna. Marine Ecology Progress Series,. V.25:83-
89.
Shouse, Michelle K., 2002, The effects of decreasing trace metal concentrations on benthic community
structure: Master's Thesis, San Francisco State University. 177pp.
Shouse, M.K., Parchaso, F., and J.K. Thompson, 2003, Near field receiving water monitoring of benthic
community near the Palo Alto Water Quality Control Plant in South San Francisco Bay: February
1974 through December 2002: U.S. Geological Survey Open File Report 03-224, 52pp.
Thomson, E.A., S.N. Luoma, C.E. Johansson, and D.J. Cain, 1984, Comparison of sediments and
organisms in identifying sources of biologically available trace metal contamination: Water
Resources, V.18, no. 6:755-765.
Thompson, J.K., and Parchaso, F., 2012, Benthic invertebrate community assessment as a phytoplankton
consumer and fish and bird prey source before and after the start of the restoration: South Bay Salt
Pond Restoration Project Cooperative Agreement #2009-0211, 90 p.
Thompson, J.K., F. Parchaso, and M.K. Shouse, 2002, Near field receiving water monitoring of benthic
community near the Palo Alto Water Quality Control Plant in South San Francisco Bay: February
1974 through December 2000: U.S. Geological Survey Open File Report 02-394, 117pp.
USEPA, 2001, Appendix to Method 1631: Total Mercury in Tissue, Sludge, Sediment, and Soil by Acid
Digestion and BrCl Oxidation: Environmental Protection Agency EPA-821-R-01-013, 13 p.
USEPA, 2002, Method 1631, Revision E: Mercury in water by oxidation, purge and trap, and cold vapor
atomic fluorescence spectrometry: U.S. Environmental Protection Agency, Office of Water EPA-821-
R-02-019, 36 p.
USEPA, 2004, Revised assessment of detection and quantitation approaches: Washington, D.C., U.S.
Environmental Protection Agency, EPA–821–B–04–005, 254 p.
22
Figure 1. Map of Palo Alto sampling site and the surrounding region. The locations where
benthic invertebrate samples and metals samples (sediments and M. petalum) will be collected are
shown in panel B.
23
Table 1. Chemical and physical data, sampling frequency (per year), and analytical methodology
proposed for monitoring the near-field discharge of the Palo Alto RWQCP.
Constituent Matrix Frequency Method
Ag Sediment and tissue 6-9 ICP-OES1
Al Sediment 6-9 ICP-OES
Cd Sediment and tissue 6-9 ICP-OES
Cr Sediment and tissue 6-9 ICP-OES
Cu Sediment and tissue 6-9 ICP-OES
Fe Sediment and tissue 6-9 ICP-OES
Hg (total) Sediment and tissue 6 Atomic fluorescence spectrometry
Mn Sediment 6-9 ICP-OES
Ni Sediment and tissue 6-9 ICP-OES
Pb Sediment and tissue 6-9 ICP-OES
Se Sediment and tissue 6 ICP-MS coupled to hydride generation
Zn Sediment and tissue 6-9 ICP-OES
Particle size Sediment 6-9 Physical separation (>100 μm & <100 μm)
TOC Sediment 6-9 IRMS2
Archive Sediment 6-9 Dry sediment storage
1 Indicatively Coupled Plasma-Optical Emission Spectrophotometry
2 Continuous Flow Isotope ratio Mass Spectrophotometry (IRMS)
Table 2. 2016-2020 Budget for Palo Alto Studies.
Activity Salary Supplies Analysis Misc. Totals
Sediment
& Tissue
Community
&
Reproduction
Sediment
& Tissue
Community Sediment
& & Tissue
Reproduction
Community
&
Reproduction
Field Work $3,850 $3,400 $500
Sample Preparation $4,950 $4,700 $600
Chemical Analyses $4,700 $975
Invertebrate
Taxonomy
$500
Reproductive Tissue
Processing
$1,000
Total Organic Carbon $800
Data Analysis $3,450 $2,000
Instrument
Maintenance/Repair
$1,600
Final Report $4,300 $1,950
SUBTOTALS $21,250 $12,050 $2,075 $800 $1,500 $1,600
DIRECT COST/Year $39,275
INDIRECT COST/Year $22,748
TOTAL COSTS 2016 $62,023
TOTAL COSTS 2017 $62,023
TOTAL COSTS 2018 $62,023
TOTAL COSTS 2019 $62,023
TOTAL COSTS 2020 $62,023
TOTAL COSTS 2016 -
2020 $310,115
24