Ecology of the San Francisco Estuary
The San Francisco Estuary together with the Sacramento-San Joaquin River Delta represents a highly altered ecosystem. The region has been heavily re-engineered to accommodate the needs of water delivery, shipping, agriculture, and most recently, suburban development. These needs have wrought direct changes in the movement of water and the nature of the landscape, and indirect changes from the introduction of non-native species. New species have altered the architecture of the food web as surely as levees have altered the landscape of islands and channels that form the complex system known as the Delta.
This article deals particularly with the ecology of the low salinity zone (LSZ) of the estuary. Reconstructing a historic food web for the LSZ is difficult for a number of reasons. First, there is no clear record of the species that historically have occupied the estuary. Second, the San Francisco Estuary and Delta have been in geologic and hydrologic transition for most of their 10,000 year history, and so describing the "natural" condition of the estuary is much like "hitting a moving target". Climate change, hydrologic engineering, shifting water needs, and newly introduced species will continue to alter the food web configuration of the estuary. This model provides a snapshot of the current state, with notes about recent changes or species introductions that have altered the configuration of the food web. Understanding the dynamics of the current food web may prove useful for restoration efforts to improve the functioning and species diversity of the estuary.
- 1 Physical geography
- 2 Hydrodynamics
- 3 Pelagic zone
- 4 Food web
- 5 Producers
- 6 Consumers
- 7 Introduced species
- 8 Summary
- 9 Future ecology
- 10 See also
- 11 Notes
- 12 References
The San Francisco Bay is both a bay and an estuary. The former term refers to any inlet or cove providing a physical refuge from the open ocean. An estuary is any physiographic feature where freshwater meets an ocean or sea. The northern portion of the bay is a brackish estuary, consisting of a number of physical embayments which are dominated by both marine and fresh water fluxes. These geographic entities are, moving from saline to fresh (or west to east): San Pablo Bay, immediately north of the Central Bay; the Carquinez Strait, a narrow, deep channel leading to Suisun Bay; and the Delta of the Sacramento and San Joaquin rivers.
Until the 20th century, the LSZ of the estuary was fringed by tule-dominated freshwater wetlands. Between 80-95% of these historic wetlands have been filled to facilitate land use and development around the Bay Area. Habitat loss at the edges of the pelagic zone is thought to create a loss of native pelagic fish species, by increasing vulnerability to predation.
The intertidal and benthic estuary is presently dominated by mudflats that are largely the result of sedimentation derived from gold mining in the Sierra Nevada in the late 19th century. The trend toward high sediment loads was reversed in the 1950s with the advent of the Central Valley Project, locking up most sediment behind dams, and resulting in an annual net loss of sediments from the estuary. Thus the mudflats appear to be slowly receding, although turbidity remains extremely high. The high turbidity of the water is responsible for the unique condition that exists in the San Francisco Estuary wherein high nutrient availability does not lead to high phytoplankton production. Instead, most algae photosynthetic organisms are light-limited.
The Delta has likewise experienced heavy alteration. Beginning in the 19th century, naturally occurring levees were reinforced for permanency, to protect farmlands from regular flooding. Many of these farms were established on peat islands occurring in the middle of the Delta waterways. Intensive farming oxidized the high carbon content of the soil, causing considerable loss of soil mass. As a consequence, these islands have subsided, or sunk, to nearly 6 meters below sea level. The Delta today consists of highly riprapped waterways, punctuated by islands that appear like "floating bowls" with their basins far below the surface of the water. These islands are at high risk for flooding due to levee collapse. The subsequent eastward shift in salinity is expected to dramatically alter the ecology of the entire LSZ of the San Francisco Estuary.
The LSZ centers around 2 psu (practical salinity units, a measurement of salinity) and ranges from about 6 psu down to 0.5 psu. The primary fresh water inputs to the estuary derive from runoff of regional precipitation, the Sacramento River, and the San Joaquin River.
River inflow is largely controlled by upstream reservoir releases. A significant fraction of this inflow is exported out of the Delta by the federal Central Valley Project and the State Water Project to southern California for agricultural and urban use. These alterations have removed much of the variation in through-estuary outflow (i. e., freshwater that makes it out the Golden Gate), creating lower outflow in the winter and higher outflow in the summer than historically found in the estuary. Phytoplankton, zooplankton, and larval and adult fish can become entrained in the export pumps, causing a potentially significant but unknown impact on the abundance of these organisms. This may be particularly true of the endangered delta smelt, a small endemic fish; unexceptional except that it has been described as being tremendously abundant in historical accounts. The delta smelt is believed to migrate and spawn upstream in the Delta during the early summer, placing its eggs and larvae at high risk for entrainment. Management for the smelt is currently the source of controversy as its ecology brings into collision course the disparate water needs of conservation, development and agriculture in California.
The movement of water out of the estuary is complex and dependent upon a number of factors. Tidal cycles cause water to move toward and away from the Golden Gate four times in a 24 hour period.
Using 2 psu as a marker for the Low Salinity Zone, the direction and magnitude of fluctuations can be tracked as its distance in kilometers from the Golden Gate, or X2. Because the position of X2 relies upon a number of physical parameters including inflow, export, and tides, its position shifts over many kilometers on a daily and seasonal cycle; over the course of a year, it can range from San Pablo Bay during high flow periods, up into the Delta during the summer drought. The position of X2 is carefully monitored and maintained by releasing water from upstream reservoirs in anticipation of export demand. This is mandated by State Water Board Decision 1641 and requires that state and federal pumping be curtailed if X2 is shifted east of Chipps Island (75 river kilometers upstream of the Golden Gate Bridge) during the months of February through May, or east of Collinsville (81 river kilometers upstream of the Golden Gate Bridge) during the months of January, June, July and August. (D-1641 pp 150)
Gravitational circulation causes stratified high salinity water at depth to flow landward while low salinity water on top flows seaward. The effect of gravitational circulation may be most pronounced during periods of high fresh water flow, providing a negative feedback for maintaining the salt field and the distribution of pelagic organisms in the estuary.
Mixing is important at the landward edge of gravitational circulation, often around X2, where the water column becomes less stratified. A fixed mixing zone occurs at the "Benicia Bump" at the east end of the Carquinez Strait, where the deep channel becomes dramatically shallower as it enters Suisun Bay. Mixing is critical in maintaining salinity such that extremely large inputs of fresh water are required to move X2 a short distance to the west. Mixing also assists pelagic organisms in maintaining position in the estuary, slowing the advection of primary and secondary production out of the system.
Pelagic organisms spend all or part of their lives in the open water, where habitat is defined not by edges but by physiological tolerance to salinity and temperature. The Low Salinity Zone (LSZ) of the San Francisco Estuary constitutes a habitat for a suite of organisms that are specialized to survive in this unique confluence of terrestrial, freshwater, and marine influences. While there are many habitats with distinct ecologies that are part of the estuary (including marine, freshwater, intertidal marsh and benthic mudflat systems) each is linked to the LSZ by export and import of freshwater, nutrients, carbon, and organisms.
The distribution and abundance of organisms in the LSZ is dependent upon both abiotic and biotic factors. Abiotic factors include the physical geography and hydrology of the estuary, including nutrient inputs, sediment load, turbidity, environmental stochasticity, climate and anthropogenic influences. Abiotic factors tend to drive production in the estuarine environment, and are mediated by biotic factors.
Biotic factors include nutrient uptake and primary production, secondary production of zooplankton, food web and trophic dynamics, energetic transfer, advection and dispersal in and out of the system, survival and mortality, predation, and competition from introduced species.
It is difficult to characterize the historic food web of the San Francisco Estuary because of the dramatic changes in geography, hydrology, and species composition that have occurred in the past century. However, monitoring begun in the 1970s gives some information about the historic dynamics of the foodweb. Prior to the 1980s the LSZ was dominated by a phytoplankton-driven foodweb, a stable mesoplankton population dominated by the copepod Eurytemora affinis, and large macrozooplankton typified by San Francisco bay shrimp and mysid shrimps. These provided nutrition and energy to native filter feeders such as the northern anchovy (Engraulis mordax), and planktivores such as delta smelt and juvenile salmon.
Food web change has been driven historically by increased turbidity, and more recently by introduced species, as described in the sections on primary and secondary production.
Notably, the high clearance rate of the introduced Amur River clam Potamocorbula amurensis population has produced a ten-fold decline in plankton density, resulting in a carbon trap in the benthos and an assumed increase in waste detrital production. This waste is hypothesized to fuel the microbial loop, resulting in an increase in microzooplankton such as the copepod Limnoithona tetraspina, which utilize rotifers and ciliates.
These changes are one cause for declining fish stocks. For example, the northern anchovy, Engraulis mordax, was until the 1980s quite abundant in the Low Salinity Zone, until its range in the estuary became restricted to the Central and South Bays. This is probably due to a behavioral response following the introduction of the Amur River (Potamocorbula amurensis) clam and the subsequent decline in plankton availability.
More recently, a general Pelagic Organism Decline (POD) was described, and this has been the source of much concern within the scientific, managerial, and political communities.
Several key species, including delta smelt, longfin smelt, striped bass, and threadfin shad have been declared "species of interest" because of a stepwise decline in abundance beginning in 2001. This was attended by a similar decline in secondary productivity and is currently the source of much research. A number of hypotheses have been proposed to explain the POD, including food web decline, water exports from the Delta, and toxics from urban, industrial, or agricultural sources.
Primary production and nutrient uptake
Primary production by phytoplankton fixes energy and key nutrients into a biologically available form (i.e., food), via photosynthesis. Phytoplankton production is largely structured by physical parameters: nutrient availability, sunlight, turbidity, and temperature.
The San Francisco Estuary has a non-limiting source of nutrients that can be used for primary production, derived largely from waste water treatment facilities, agricultural and urban drainage, and the ocean. In spite of this, the estuary is unique in that it tends to have a relatively depressed rate of primary production. This is probably due to two factors: large inputs of nitrogen in the form of ammonium, which suppresses nitrate uptake by phytoplankton, which prefer the metabolically cheaper NH4+, and high turbidity, which limits light required for photosynthesis to the top few centimeters of the water column. This turbidity is a legacy of hydraulic gold mining in the Sierra Nevada in the 1850s.
High residence time of water in the estuary tends to allow phytoplankton biomass to accumulate, increasing density, while low residence time removes phytoplankton from the estuary. The latter is typical of the main channels of the estuary during periods of high flow, when surface waters tend to flush particles and plankton downstream.
Herbivory also removes phytoplankton from the water column. While the pelagic food web is based upon phytoplankton production, most of this production is diverted to the benthos via predation by the introduced Amur River clam (Corbula amurensis). Levels of phytoplankton biomass declined by an order of magnitude after the widespread introduction of C. amurensis in the mid-1980s, and have not rebounded.
The main source of photosynthetically derived energy is phytoplankton. Generally speaking, diatoms and microflagellates produce most of the bioavailable carbon in the estuary. Other types, notably the dinoflagellates, may produce harmful algal blooms, or red tides, that are less readily available for assimilation into the foodweb.
Primary production from phytoplankton is a function of two different factors: growth rates and accumulation (Fig. 1). Although the LSZ is a sink for high concentrations of nutrients from urban and agricultural sources, phytoplankton production rates are quite low. Nitrate is optimally used by phytoplankton for growth, but ammonium (largely derived from sewage outfalls) has a suppressive effect on growth rate. Thus, while not nutrient limited, phytoplankton tend to grow more slowly due to the kinds of nitrogen present. Another suppressive factor on growth rate is the high turbidity of the estuary, which limits the ability of photosynthetically active radiation (PAR) to penetrate beyond the top few centimeters of the water column. This limits phytoplankton photosynthesis to a relatively shallow photic zone. Thus, when the water column is stratified, turbidity is high, and ammonium is present, the growth rate of phytoplankton is typically suppressed.
Phytoplankton accumulation is primarily the result of residence time. The north Delta and Suisun Bay have relatively low residence times due to the high volume of water moving through the region for downstream flow and for export to southern California. Since water moves more rapidly through this part of the system, the rate of accumulation decreases as productivity is advected out of the system. In contrast, parts of the southern Delta have a higher residence time due to the low volume of water moving through the system; in fact the water on occasion runs backwards, due to the lack of inflow from the San Joaquin River, and export pumping. During summer, phytoplankton density may be an order of magnitude higher here than in other parts of the estuary.
Harmful algal blooms (HAB's) of dinoflagellates or cyanobacteria produce toxic metabolic byproducts that render them noxious to many organisms. Fostered by a combination of high nutrient concentrations and temperatures, HAB's have a doubly negative affect on the food web by competitively excluding diatoms and microflagellates, further reducing bioavailable primary production. While certain invertebrates such as bivalves may not be directly affected, they may propagate toxins up the food chain, sickening or killing predators. It is not well understood how copepods are affected. The invasive algae Microcystis aeruginosa is now common in the Delta during summer months and may reduce copepod productivity (in addition to being potentially carcinogenic for humans).
Enormous quantities of sediment and detritus flux through the LSZ. Much of this is organic debris in the form of dissolved and particulate organic matter (DOM and POM, respectively). In addition to upstream sources, organic matter may accumulate from local organism mortality and waste production.
Detritivores capitalize upon this energy source, creating an alternate and parallel food web of potentially large importance. This is because carbon fixation into the detrital food web is not limited by stratification, turbidity or day length, all of which limit photosynthesis. Detrital production occurs continuously, limited only by inputs and advection out of the Delta system.
Bacteria are the chief agents of transformation of DOM and POM into bioavailable carbon through the microbial loop. This mechanism is particularly important in nutrient limited marine systems, where bacteria release nutrients from sinking detritus, allowing it to be recycled back to the photic zone. Little work has been applied to the function of the microbial loop in the San Francisco Estuary, but it may be that the role of bacteria is not critical for recycling nutrients in a eutrophic system. Rather, they may provide an alternative food chain through direct grazing by flagellates, rotifers and ciliates.
The high abundance of the cyclopoid copepod Limnoithona tetraspina may be due to its reliance on ciliates rather than phytoplankton as a primary food source. The major species of calanoid copepods may also use ciliates as a supplementary or even primary food source, but to what degree is unknown.
Secondary production refers to organisms that feed on primary production and transfer energy to higher trophic levels of the estuarine foodweb. Historically, secondary production in the San Francisco Estuary was dominated by mysid shrimp production. However, the native mysid Neomysis mercedis has been largely replaced by the introduced Acanthomysis bowmani, which persists at lower densities. The introduced amphipod Gammurus daiberi may have taken over some of this niche, but it is largely restricted to fresh water.
Today, the main source of secondary production derives from copepods. The naturalized native calanoid copepod Eurytemora affinis is believed to have been introduced near the end of 19th Century. It dominated the zooplankton of the low salinity zone until the 1980s when it was largely replaced by another introduced calanoid copepod, Pseudodiaptomus forbesi. P. forbesi persists by maintaining a source population in freshwater, high-residence regions of the estuary, particularly in the Delta, outside the range of salinity tolerance of the Amur River clam. Because the once-dominant E. affinis lacks an upstream range, it is more vulnerable to predation by the clam, and suffers from apparent competition with P. forbesi.
Other calanoid copepods that may be of significance are the recently introduced Sinocalanus doerri and Acartiella sinensis. Little is known about the life histories of these organisms, although based upon their morphology, they may prey on other copepods. They appear in irregular cycles of abundance, during which they may dominate the zooplankton.
Yet another invasive copepod, the very small cyclopoid Limnoithona tetraspina, appeared in the Low Salinity Zone in the 1990s. Since then, L. tetraspina has become the numerically dominant copepod, reaching densities on the order of 10,000/m3. It relies on the microbial loop as its food source, feeding upon bacteria, ciliates and rotifers. In addition, it seems invulnerable to predation by the Amur River clam, for reasons that are unknown. Because of its small size, L. tetraspina is generally not available for consumption by larger predators, particularly fish, making it an energetic dead end.
Primary consumers rely upon primary production as a main food source. The most important consumers of the pelagic web of the LSZ are copepods, along with the rotifers, flagellates and ciliates mentioned above. All species of calanoid copepods have declined under high predation pressure from the recently introduced Amur River clam (Corbula amurensis). Because of this, and because copepods rely upon both photosynthetic and detrital food sources, copepods in the LSZ have limited feedback on primary production, unlike marine and lentic systems where copepods can graze down blooms in a matter of days.
Pseudodiaptomus forbesi is the dominant calanoid copepod of the LSZ in terms of biomass. It has a sufficiently wide salinity tolerance that it can persist both at low salinity and in fresh water. This wide distribution helps the population maintain an upstream refuge from predation, unlike other species with narrower salinity tolerances.
Limnoithona tetraspina has become the numerically dominant cyclopoid copepod since its introduction in 1993. It feeds primarily upon ciliates and microflagellates, but unlike P. forbesi, it is relatively impervious to predation by clams or fish, hence its abundance. Energetically, L. tetraspina may be a dead end for the food web; these copepods are either advected out of the system by tides and currents, or die and fall down to the benthos, where they may be available to the microbial loop, or to detritivores.
A number of predatory copepods exist throughout the Delta, about which relatively little is known. Sinocalanus doerri, Acartiella sinensis, and Tortanus dextrilobatus all appear to be morphologically capable of predation upon other copepods. Each was introduced to the estuary, probably through ballast water exchange since the 1980s. Generally, they are not in sufficient abundance to negatively impact copepod consumers; however, periodic blooms of S. doerri and A. sinensis occur which have not been well studied.
While capable of filter-feeding, mysids (tiny shrimp-like creatures) are largely carnivorous, feeding on copepod adults. They provided an energetic conduit between plankton and planktivorous fishes, including juvenile fishes, sturgeon, Chinook salmon, and American shad. Mysids were once abundant until the native Neomysis mercedis was replaced in the mid-1980s by the invasive Acanthomysis bowmani, which is smaller and less abundant. Mysid decline has been linked to the subsequent decline in a number of fish species in the estuary in the 1980s and '90s.
Shrimp are generalist carnivores who prey largely on mysids and amphipods. Crangon franciscorum represents one of two remaining commercial fisheries in the estuary. While no longer used for "San Francisco Bay Shrimp Cocktails", they are harvested for bait. Other predators include striped bass and Chinook salmon adults and smolts.
Because fish are a taxonomically and morphologically diverse group, species vary in their trophic ecologies. In general, fish can be divided into four broad feeding categories: filter feeders, planktivores, piscivores and benthic feeders.
Filter feeders strain the water column indiscriminately for small prey, typically phyto- and zooplankton. This category of fishes includes threadfin shad (Dorosoma petenense), American shad (Alosa sapidissima), inland silversides (Menidia beryllina), and anchovies (Engraulis mordax). Some evidence suggests that some of these species are food-limited due to the depressed levels of plankton after the introduction of the Amur River clam. Anchovies have left the LSZ in favor of more productive regions of the estuary in the San Pablo and Central Bays.
Planktivores selectively prey upon individual zooplankton, such as copepods, mysids and gammarids. This group includes most fish larvae, delta smelt (Hypomesus transpacificus) and longfin smelt (Spirinchus thaleichthys), tule perch (Hysterocarpus traski), and salmon smolts. The delta smelt is of particular interest due to its endangered status. It may be food-limited, but the evidence is somewhat contradictory. Other factors, such as entrainment of eggs and larvae in the export pumping of fresh water from the Delta may also explain the decline.
The main piscivore of the LSZ is the striped bass (Morone saxatilis), which was introduced in the 1890s and preys heavily upon native fishes. Striped bass are an important sport fishery in the San Francisco Estuary, and as such, represent a minor withdrawal of biomass from the estuary.
Benthic, or bottom-dwelling, fishes include white sturgeon (Acipenser transmontanus), white catfish (Ameiurus catus), and starry flounder (Platichthys stellatus). Because of their habitat orientation, they feed primarily on epibenthic organisms such as amphipods, bay shrimp, and bivalves. These fish are known to feed at least occasionally on the Amur River clam, which would represent one of the few channels for energy flow from that species, except for detrital production.
The sole commercial fishery in the LSZ is for bait shrimp. There are a variety of sports fisheries that represent a minor flow of carbon, but significant flows of capital to local economies around the estuary. Most of the recreational fisheries surround striped bass, sturgeon, and introduced fresh water basses in the freshwater Delta. This paucity of fisheries makes the San Francisco Estuary unique. Nearly all estuaries worldwide support at least remnants of significant fisheries. The San Francisco Estuary at one time supported major fisheries for salmon, anchovies, and Dungeness crabs until the 1950s. The demise of these fisheries was probably due more to habitat loss than overharvesting.
The San Francisco Estuary is a major stop on the Pacific flyway for migrating waterfowl. Yet little is known about the flow of carbon in or out of the estuary via birds. Millions of waterfowl annually use the bay shallows as a refuge. Most of the birds are dabbling ducks that feed on submerged aquatic vegetation. Diving ducks (such as scaups) feed on epibenthic organisms like C. amurensis, representing a possible flow of carbon from that otherwise dead end. Two endangered species of birds are found here: the California least tern and the California clapper rail. Exposed bay muds provide important feeding areas for shorebirds, but underlying layers of bay mud pose geological hazards for structures near many parts of the bay perimeter. Piscivorous birds such as cormorants and pelicans also inhabit the estuary, but their trophic impact remains poorly studied.
Before 1825, Spanish, French, English, Russians and Americans were drawn to the Bay Area to harvest prodigious quantities of beaver (Castor canadensis), river otter, marten, fisher, mink, fox, weasel, harbor and fur seals (Callorhinus ursinus) and sea otter (Enhydra lutris). This early fur trade, known as the California Fur Rush, was more than any other single factor, responsible for opening up the West and the San Francisco Bay Area, in particular, to world trade. By 1817 sea otter in the area were practically eliminated. The Russians maintained a sealing station in the nearby Farallon Islands from 1812 to 1840, taking 1,200 to 1,500 fur seals annually, though American ships had already exploited the islands. By 1818 the seals diminished rapidly until only about 500 could be taken annually and within the next few years, the fur seal was extirpated from the islands until they began to recolonize the islands in 1996. Although twentieth century naturalists were skeptical that beaver were historically extant in coastal streams or the Bay itself, earlier records show that the California Golden beaver (Castor canadensis ssp. subauratus) was one of the most valued of the animals taken, and apparently was found in great abundance. Thomas McKay reported that in one year the Hudson's Bay Company took 4,000 beaver skins on the shores of San Francisco Bay. Recently, beaver have recolonized the brackish Napa Sonoma Marsh in north San Pablo Bay and its Sonoma Creek and Napa River tributaries. Also recently re-colonizing the Bay and its tributaries, the North American River Otter (Lontra canadensis) was first reported in Redwood Creek at Muir Beach in 1996, and recently in Corte Madera Creek, and in the south Bay on Coyote Creek, as well as in 2010 in San Francisco Bay itself at the Richmond Marina.
Jellyfish have not been prevalent in the estuary until recently. In East Coast estuaries such as Chesapeake Bay, they are often top-level predators, feeding indiscriminately on both fish and zooplankton. Several small invasive taxa have been identified in the LSZ and freshwater regions. These species strobilate in summer, but maintain polyps in the benthos year round.
Their impact on the plankton is unknown, but research is underway to quantify it. In sufficient density, jellies may have a complementary role to C. amurensis in suppressing zooplankton, by inhabiting areas of low salinity outside the range of the clams, where planktonic species have had a predation-free refuge.
The benthic community has taken on a disproportionately large role in the food web ecology of the estuary due to key invasions by bivalves. The use of these clams, the Amur River clam (Corbula amurensis) has a wide salinity tolerance that extends into the low salinity zone, but not into freshwater. It filter feeds on phytoplankton and small zooplankton, such as calanoid copepod nauplii. The clam has few predators in the San Francisco Estuary and this allows it to grow to high densities (on the order of tens of thousands/m2). Because of its high clearance rates, it is capable of clearing the entire water column of portions of the estuary in a few days, leading to drastically depleted plankton populations. This is thought to be the main cause of a decline in ecosystem productivity after the invasion of the clams in the mid-1980s.
This decline in productivity is essentially due to the redirection of the pelagic network to a benthic chain by this one species. BecaRiver clam feeds on primary producers, consumers and predators, it impacts multiple trophic levels. Consequently, nearly all plankton exhibit signs of apparent competition, in that production at one trophic level impacts all others by increasing clam abundance. This results in a negative feedback loop: C. amurensis limits plankton biomass, which in turn limits C. amurensis. However, inputs from outside the system due to tidal advection or upstream sources may increase C. amurensis biomass, further driving plankton limitation. This feedback loop is further amplified because the clam may persist for more than one or two years, which puts added pressure on plankton populations during cycles of low productivity.
The redirection of carbon by C. amurensis to the benthos has created a limited chain, leaving the pelagic web depauperate. Detrital production from clam excretion and death may fuel bacterial production, which may be circulated into the detrital food web, or microbial loop.
While the recycled nutrients may support some phytoplankton growth, it ultimately feeds back to increased C. amurensis populations. The recent invasion success of Limnoithona tetraspina may be understood in terms of this phenomenon. It feeds on ciliates and microflagellates which are too small to be grazed by the clam, thereby avoiding competition. Additionally, L. tetraspina appears impervious to predation by the clam or (almost) anything else. The rise of the microbial food web and the invasion of L. tetraspina capitalize are the result of an untapped alternative path for energy flow in the food web, facilitated by C. amurensis. Subsequent patterns of invasion may reflect a similar pattern.
Species introductions have been increasing since at least the 19th Century as a function of increasing trade and traffic. Introductions include numerous taxa, including copepods, shrimp, amphipods, bivalves, fish and both rooted and floating plants. Many pelagic species have been introduced most recently through ballast water releases from large ships directly into the estuary. As a result, many of these introduced species originate from estuaries around the Pacific Rim, particularly copepods such as P. forbesi and L. tetraspina. The Amur River clam originates from Asia, and has created significant and drastic changes to the ecology of the LSZ, primarily by diverting pelagic food to the benthos and into an accelerated microbial loop.
Species have also been introduced via attachment to sporting boats which are trailered between regions. This is the probable source of a number of low salinity plants like Egeria densa and water hyacinth (Eichhornia crassipes). These plants have created profound changes in the Delta by disrupting water flow, shading phytoplankton, and providing habitat for piscivorous fish like the striped bass, Morone saxatilis, itself intentionally introduced in the late 1800s from the Chesapeake Bay. The freshwater quagga mussel, originally from Europe, is expected to be introduced by boaters within the next two to ten years, in spite of precautionary measures.
The modern food web is derived from a series of invasions and trophic substitutions.
This process is expected to continue, as new organisms arrive through accidental or intentional introductions. What is less clear is the extent to which previous introductions pave the way for future invasions. This may occur in one of three ways.
- An early invader may provide a resource that is unutilized in the new system until a new predator is introduced (L. tetraspina and the microbial loop, as described above).
- Early invaders may facilitate new ones by altering habitat and making it suitable for subsequent invasions (jelly polyps using Amur River clam shells for substrate).
- Apparent competition between old and new residents may increase the possibilities for invasion and settlement of new organisms that can capitalize on unexploited resources (the subsidization of the Amur River clam by upstream populations of the introduced copepod P. forbesi, creating pressure on native copepods).
The LSZ food web of the San Francisco Estuary operates in two parallel and asymmetrical directions. The bulk of carbon is assimilated into the benthic and microbial loops, which represent energetic dead ends. A smaller fraction is delivered to higher pelagic trophic levels which may support copepods, fish, birds and fisheries. This redirection of the food web into these two narrow loops may be responsible for the decline in macroinvertebrates and fishes in the estuary, which operate outside of these chains. Restoration of the estuary to a higher degree of function relies upon the probability of delivering increased benefits to the pelagic web without subsidizing the benthic.
The ecology of the Low Salinity Zone of the San Francisco Estuary is difficult to characterize because it is the result of a complex synergy of both abiotic and biotic factors. In addition, it continues to undergo rapid change resulting from newly introduced species, direct anthropogenic influences and climate change. Future ecological changes will be driven on an ecosystem wide scale, particularly as sea level rise, tectonic instability and infrastructure decline cause levy failure in the Delta. The resulting back-surge in water flow is expected to force X2 into the Delta, jeopardizing spatially oriented habitat (like freshwater marshes), channelizing the low salinity zone, and threatening southern California's water supply, with unknown and unforeseeable consequences for the natural and human ecology of the West coast's largest estuary.
- List of watercourses in the San Francisco Bay Area
- Hydrography of the San Francisco Bay Area
- The Watershed Project
- San Francisco Estuary and Watershed Science
- Kimmerer 2004
- Conomos 1979
- Vayssieres 2006
- Jassby 2000
- Deverel 1998
- Philip 2007
- Lund 2007
- Kimmerer 2002
- Moyle 1992
- Bennett 2006
- Monismith 1996
- Burau 1998
- Schoellhamer 2001
- Orsi 1986
- Kimmerer 1996
- Kimmerer 2006
- Taugher 2005
- Smith 2002
- Dugdale 2003
- Jassby 2002
- Nichols 1986
- Kimmerer 1994
- Jassby and Cloern 2000
- Anderson et al. 2002
- Jassby et al. 2002
- Dugdale et al. 2003
- Cloern 1987
- Cole and Cloern 1987
- Ball and Arthur 1979
- Lehman and Waller 2003
- Murrell et al. 1999
- Murrell and Hollibaugh 2000
- Jassby et al. 1993
- Hollibaugh and Wong 1996
- Bouley 2006
- Rollwagen-Bollens and Penry 2003
- Rollwagen-Bollens et al. 2006
- Modlin 1997
- Kimmerer 1998
- Lee 1999
- Orsi 1991
- Orsi 1999
- Bouley and Kimmerer 2006
- Orsi and Ohtsuka 1999
- Orsi and Knutson 1979
- Modlin and Orsi 1997
- Sitts and Knight 1979
- Radovich 1963
- Peterson 1997
- Nichols et al. 1986
- Poulton et al. 2002
- Richman and Lovvorn 2004
- Skinner, John E. (1962). An Historical Review of the Fish and Wildlife Resources of the San Francisco Bay Area (The Mammalian Resources). California Department of Fish and Game, Water Projects Branch Report no. 1. Sacramento, California: California Department of Fish and Game.
- Suzanne Stewart and Adrian Praetzellis (November, 2003). Archeological Research Issues for the Point Reyes National Seashore - Golden Gate National Recreation Area (Report). Anthropological Studies Center, Sonoma State University. p. 335. http://www.sonoma.edu/asc/projects/pointreyes/overview4.pdf. Retrieved Jan 10, 2010.
- Thompson, R. A. (1896). The Russian Settlement in California Known as Fort Ross, Founded 1812...Abandoned 1841: Why They Came and Why They Left. Santa Rosa, California: Sonoma Democrat Publishing Company. p. 7. ISBN 0-559-89342-6.
- White, Peter (1995). The Farallon Islands: Sentinels of the Golden Gate. San Francisco, California: Scottwall Associates. ISBN 0-942087-10-0.
- Tappe, Donald T. (1942). "The Status of Beavers in California". Game Bulletin No. 3 (California Department of Fish & Game).
- "Get Outside!". San Francisco Chronicle. April 1966. Retrieved 2011-03-06.
- "Blue Oak Ranch Reserve". University of California. Retrieved 2011-03-06.
- Werner and Hollibaugh 1993
- Carlton et al. 1990
- Nichols et al. 1990
- Carlton 1996
- Cole 1992
- Dey 2007
- Epstein 2006
- Anderson, D. M., P. M. Glibert, and J. M. Burkholder. 2002. Harmful Algal Blooms and Eutrophication: Nutrient Sources, Composition, and Consequences. Estuaries 25:704-726.
- Ball, M. D., and J. F. Arthur. 1979. Planktonic chlorophyll dynamics in the northern San Francisco Bay and Delta. Pages 265-286 in T. J. Conomos, editor. San Francisco Bay: The urbanized estuary. American Association for the Advancement of Science, Pacific Division, San Francisco, CA.
- Bennett, W. A. (2006). Delta Smelt Growth and Survival During the Recent Pelagic Organism Decline: What Causes Them Summer Time Blues? CALFED Science Conference. Sacramento, CA.
- Bouley P., W. J. K. (2006). "Ecology of a highly abundant, introduced cyclopoid copepod in a temperate estuary. " Marine Ecology Progress Series 324: 219-228.
- Burau, J. R. (1998). "Results from the hydrodynamic element of the 1994 entrapment zone study in Suisun Bay, Sacramento, CA. " Interagency Ecological Program for the San Francisco Bay-Delta Estuary Technical Report 56: 13-62.
- Carlton, J. T., J. K. Thompson, L. E. Schemel, and F. H. Nichols. 1990. Remarkable invasion of San Francisco Bay (California, USA) by the Asian clam Potamocorbula amurensis. 1. Introduction and dispersal. Marine Ecology Progress Series. 66:81-94.
- Carlton, J. (1996). "Biological Invasions and Cryptogenic Species. " Ecology 77(6).
- Cole, B. E., and J. E. Cloern. 1987. An empirical model for estimating phytoplankton productivity in estuaries. Marine Ecology Progress Series. 36:299-305.
- Cole, B. E., J. K. Thompson, and J. E. Cloern (1992). "Measurement of filtration rates by infaunal bivalves in a recirculating flume. " Marine Biology 113: 219-225.
- Cloern, J. E. 1987. Turbidity as a control on phytoplankton biomass and productivity in estuaries. Continental Shelf Research 7:1367-1381.
- Conomos, T. J., Ed. (1979). San Francisco Bay: The urbanized estuary. San Francisco, CA, Pacific Division, American Association for the Advancement of Science.
- Deverel, S. (1998). Subsidence mitigation in the Sacramento-San Joaquin Delta., CALFED Bay-Delta Program.
- Dey, R. (2007, January 16, 2007). "Invasive Mussel Update from Lake Mead National Recreation Area. " 100th Meridian Initiative, from http://100thmeridian. org/mead. asp.
- Dugdale, R. C., V. Hogue, A. Marchi, A. Lassiter, and F. Wilkerson. 2003. Effects of anthropogenic ammonium input and flow on primary production in the San Francisco Bay. CALFED Science Program, Sacramento, CA.
- Durand, J. (2006). Determinants of calanoid copepod recruitment failure in the San Francisco Estuary Calfed Science Program. Sacramento, CA.
- Epstein, E. (2006). Creaky levees ripe for disaster. San Francisco Chronicle. San Francisco.
- Hollibaugh, J. T., and P. S. Wong. 1996. Distribution and activity of bacterioplankton in San Francisco Bay. Pages 263-288 in J. T. Hollibaugh, editor. San Francisco Bay: The ecosystem. American Association for the Advancement of Science, San Francisco, CA.
- Jassby, A. D., J. E. Cloern, and B. E. Cole. 2002. Annual primary production: Patterns and mechanisms of change in a nutrient-rich tidal ecosystem. Limnology and Oceanography 47:698-712.
- Jassby, A. D., J. E. Cloern, and T. M. Powell. 1993. Organic carbon sources and sinks in San Francisco Bay - variability induced by river flow. Marine Ecology Progress Series. 95.
- Jassby, A. D., and J. E. Cloern. 2000. Organic matter sources and rehabilitation of the Sacramento-San Joaquin Delta (California, USA). Aquatic Conservation: Marine and Freshwater Ecosystems 10:323-352.
- Jassby, A. D., J. E. Cloern and B. E. Cole. (2002). "Annual primary production: Patterns and mechanisms of change in a nutrient-rich tidal ecosystem. " Limnology and Oceanography 47(3): 698-712.
- Kimmerer, W. J., E. Gartside, and J. J. Orsi. (1994). "Predation by an introduced clam as the likely cause of substantial declines in zooplankton of San Francisco Bay. " Mar. Ecol. Prog. Ser. 113: 81-93.
- Kimmerer, W. J., J. J. Orsi. 1996. Changes in the zooplankton of the San Francisco Bay estuary since the introduction of the clam Potamocorbula amurensis. Pages 403-425 in J. T. Hollibaugh, editor. San Francisco Bay: The Ecosystem. American Association for the Advancement of Science, San Francisco, CA.
- Kimmerer, W. J., J. R. Burau, and W. A. Bennett. (1998). "Tidally oriented vertical migration and position maintenance of zooplankton in a temperate estuary. " Limnol. Oceanogr. 43(7): 1697-1709.
- Kimmerer, W. J. (2002). "Physical, biological, and management responses to variable freshwater flow into the San Francisco Estuary. " Estuaries 25: 1275-1290.
- Kimmerer, W. (2004). "Open water process of the San Francisco Estuary: from physical forcing to biological responses. " San Francisco Estuary and Watershed Science 2(1).
- Kimmerer, W. (2006). "Response of anchovies dampens effects invasive bivalve Corbula amurensis on San Francisco Estuary foodweb. " Marine Ecology Progress Series 324: 207-218.
- Lee, C. E. (1999). "Rapid and repeated invasions of fresh water by the copepod Eurytermora affinis. " Evolution 53(5): 1423-1434.
- Lehman, P. W., and S. Waller. 2003. Microcystis blooms in the delta. IEP Newsletter 16:18-19.
- Lund, J., E. Hanak, W. Fleenor, R. Howitt, J. Mount, P. Moyle (2007). Envisioning Futures for the Sacramento-San Joaquin Delta. San Francisco, Public Policy Institute.
- Modlin, R. F., and J. J. Orsi (1997). "Acanthomysis bowmani, a new species, and A. asperali, Mysidacea newly reported from the Sacramento-San Joaquin Estuary, California (Crustacea: Mysidae). " Proceedings of the Biological Society of Washington 110(3): 439-446.
- Monismith, S. G., J. R. Burau, and M. Stacey (1996). Stratification dynamics and gravitational circulation on northern San Francisco Bay. San Francisco Bay: The ecosystem. J. T. Hollibaugh. San Francisco, CA, American Association for the Advancement of Science: 123-153.
- Moyle, P. B., B. Herbold, D. E. Stevens, and L. W. Miller. (1992). "Life history and status of delta smelt in the Sacramento-San Joaquin Estuary, California. " Trans. Am. Fish. Soc. 121: 67-77.
- Murrell, M. C., J. T. Hollibaugh, M. W. Silver, and P. S. Wong. 1999. Bacterioplankton dynamics in northern San Francisco Bay: Role of particle association and seasonal freshwater flow. Limnology and Oceanography. 44:295-308.
- Murrell, M. C., and J. T. Hollibaugh. 2000. Distribution and composition of dissolved and particulate organic carbon in northern San Francisco Bay during low flow conditions. Estuarine Coastal and Shelf Science 51:75-90.
- Nichols, F. H., J. E. Cloern, S. Luoma, and D. H. Peterson. 1986. The modification of an estuary. Science 231:567-573.
- Nichols, F. H., J. K. Thompson, and L. E. Schemel. 1990. Remarkable invasion of San Francisco Bay (California, USA) by the Asian clam Potamocorbula amurensis. 2. Displacement of a former community. Marine Ecology Progress Series. 66:95-101.
- Orsi, J. J., and A. C. Knutson. 1979. The role of mysid shrimp in the Sacramento-San Joaquin Estuary and factors affecting their abundance and distribution. Pages 401-408 in T. J. Conomos, editor. San Francisco Bay: the urbanized estuary. American Association for the Advancement of Science, Pacific Division, San Francisco.
- Orsi, J. J., and W. L. Mecum. (1986). "Zooplankton distribution and abundance in the Sacramento-San Joaquin Delta in relation to certain environmental factors. " Estuaries 9(4 B): 326-339.
- Orsi, J. J., and T. C. Walter. (1991). "Pseudodiaptomus forbesi and P. marinus (Copepoda: Calanoida), the latest copepod immigrants to California's Sacramento-San Joaquin Estuary. " Bull. Plankton Soc. Japan Spec. Vol. (Proceedings of the Fourth International Conference on Copepoda): 553-562.
- Orsi, J. J., and S. Ohtsuka. (1999). "Introduction of the Asian copepods Acartiella sinensis, Tortanus dextrilobatus (Copepoda: Calanoida), and Limnoithona tetraspina (Copepoda: Cyclopoida) to the San Francisco Estuary, California, USA. " Plank. Bio. Ecol. 46: 128-131.
- Peterson, H. 1997. Clam-stuffed sturgeon. IEP Newsletter 9:19-19.
- Philip, T. (2007). A time to deliver water solutions. Sacramento Bee. Sacramento, CA.
- Poulton, V. K., J. R. Lovvorn, and J. Y. Takekawa. 2002. Clam density and scaup feeding behavior in San Pablo Bay, California. The Condor. 104:518-527.
- Radovich, J. (1963). "Effects of ocean temperature on the seaward movement of striped bass, Roccus saxatilis, on the Pacific coast. " California Department of Fish and Game 49: 191-205.
- Richman, S. E., and J. R. Lovvorn. 2004. Relative foraging value to lesser scaup ducks of native and exotic clams from San Francisco Bay. Ecological Applications 14:1217-1231.
- Rollwagen-Bollens, G. C., and D. L. Penry. 2003. Feeding dynamics of Acartia sp. in a large, temperate estuary (San Francisco Bay, CA). Marine Ecology Progress Series 257:139-158.
- Rollwagen-Bollens, G., S. Gifford, A. Slaughter, and S. M. Bollens. 2006. Protists in a Temperate Estuary: Diversity, Grazing and Consumption by Metazoans. Eos, Transactions of the American Geophysical Union, Ocean Sciences Meeting Supplement. 87:36 OS11D-05.
- Schoellhamer, D. H. (2001). Influence of salinity, bottom topography, and tides on locations of estuarine turbidity maxima in northern San Francisco Bay. Coastal and Estuarine Fine SedimentProcesses. W. H. McAnally and A. J. Mehta. Amsterdam, Netherlands, Elsevier: 343-356.
- Sitts R. M., A. W. Knight. 1979. Predation by the estuarine shrimps Crangon franciscorum Stimpson and Palaemon macrodactylus Rathbun. Biological Bulletin 156:356-368.
- Smith, S. V., and J. T. Hollibaugh (2002). "Water, salt, and nutrient exchanges in the San Francisco Bay. " Interagency Ecological Program for the San Francisco Bay-Delta Estuary TechnicalReport 66.
- Taugher, Mike (2005). Environmental sirens in Delta are screaming. Contra Costa Times.
- Trott, J. S. S., Warren J. Ferguson, and Andrew J. Kleinfeld, (2006). Central Delta Water Agency v. Bureau of Reclamation. United States Court of Appeals for the Ninth Circuit. San Francisco, CA.
- Vayssieres, M. P. (2006). Trends in the benthos of the upper San Francisco Esutary. CALFED Science Conference. Sacramento, CA.
- Werner, I., and J. T. Hollibaugh. 1993. Potamocorbula amurensis (Mollusca, Pelecyopoda): Comparison of clearance rates and assimilation efficiencies for phytoplankton and bacterioplankton. Limnology and Oceanography 38:949-964.