Low dissolved oxygen (DO) is a common feature of many estuarine and shallow-water environments, and is often attributed to anthropogenic nutrient enrichment from terrestrial-fluvial pathways. However, recent events in the U.S. Pacific Northwest have highlighted that wind-forced upwelling can cause naturally occurring low DO water to move onto the continental shelf, leading to mortalities of benthic fish and invertebrates. Coastal estuaries in the Pacific Northwest are strongly linked to ocean forcings, and here we report observations on the spatial and temporal patterns of oxygen concentration in the Columbia River estuary. Hydrographic measurements were made from transect (spatial survey) or anchor station (temporal survey) deployments over a variety of wind stresses and tidal states during the upwelling seasons of 2006 through 2008. During this period, biologically stressful levels of dissolved oxygen were observed to enter the Columbia River estuary from oceanic sources, with minimum values close to the hypoxic threshold of 2.0 mg L−1. Riverine water was consistently normoxic. Upwelling wind stress controlled the timing and magnitude of low DO events, while tidal-modulated estuarine circulation patterns influenced the spatial extent and duration of exposure to low DO water. Strong upwelling during neap tides produced the largest impact on the estuary. The observed oxygen concentrations likely had deleterious behavioral and physiological consequences for migrating juvenile salmon and benthic crabs. Based on a wind-forced supply mechanism, low DO events are probably common to the Columbia River and other regional estuaries and if conditions on the shelf deteriorate further, as observations and models predict, Pacific Northwest estuarine habitats could experience a decrease in environmental quality.
Citation: Roegner GC, Needoba JA, Baptista AM (2011) Coastal Upwelling Supplies Oxygen-Depleted Water to the Columbia River Estuary. PLoS ONE 6(4): e18672. https://doi.org/10.1371/journal.pone.0018672
Editor: Juan A. Añel, Universidade de Vigo, Spain
Received: September 27, 2010; Accepted: March 15, 2011; Published: April 20, 2011
This is an open-access article, free of all copyright, and may be freely reproduced, distributed, transmitted, modified, built upon, or otherwise used by anyone for any lawful purpose. The work is made available under the Creative Commons CC0 public domain dedication.
Funding: Funding was provided by the Bonneville Power Association (GCR) and the National Science Foundation (JN and AMB) through the Science and Technology Center for Coastal Margin Observation and Prediction (OCE-0424602). The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Low dissolved oxygen (DO) in aquatic and marine systems is an established and growing concern worldwide . Many recent papers have reported increases in the occurrence and extent of areas affected by low DO events , and the deleterious effects of low DO are well-documented on scales ranging from individual organisms to entire ecosystems . Oxygen-depleted conditions in estuarine and shallow marine areas are often attributed to anthropogenic nutrient enrichment delivered by terrestrial-fluvial pathways . Subsequent phytoplankton production and eventual decomposition by heterotrophic bacterial consumption can reduce dissolved oxygen in bottom waters. However, low DO conditions also occur naturally in subsurface waters of the worlds' oceans , , and wind-forced upwelling can propel this water onto continental shelves and into shallow water bays and estuarine systems , .
Oxygen is a non-conservative tracer, as its concentration is affected by many factors, including photosynthesis and respiration, and exchange rates between surface waters and the atmosphere or bottom waters and the benthos. Dissolved oxygen levels can vary from supersaturated to anoxic (0% saturation), often over short (semidiurnal) temporal and narrow (meter) spatial scales (e.g., , ). Supersaturated conditions are usually caused by photosynthetic production during daylight. The critical concentration delimiting hypoxia is often defined at <2.0 mg L−1 (1.4 mL L−1; ∼30% atmospheric saturation) , . While mass mortalities are a major consequence of hypoxic conditions, for many organisms the negative effects of low DO occur well above the 2.0 mg L−1 threshold –. Such sublethal effects include stress-related reductions in growth and reproduction, motility, feeding rates, and altered predator-prey relationships , , . Bricker et al.  define “biological stress” as oxygen concentrations between 2.0 and 5.0 mg L−1. Breitburg et al.  define hypoxia “mechanistically as oxygen concentrations that are sufficiently reduced that they affect the growth, reproduction, or survival of exposed animals, or result in avoidance behaviors.” It has become clear that sublethal effects must be considered when assessing the impacts of low DO events on ecosystems.
The oceanography of Northeast Pacific coastal waters is strongly influenced by wind-forced upwelling dynamics , . During upwelling, equatorward winds draw nutrient-rich, and often reduced DO, subsurface water into the photic zone, where phytoplankton growth is stimulated. Oceanographic observations have routinely detected reduced DO levels in deep water year-round, but also in shallower shelf waters during active upwelling , –. On occasion, these upwelled waters are severely hypoxic. Recently, hypoxia and mass mortalities of benthic invertebrates and fish were observed on the Oregon shelf, and these phenomena were attributed to both upwelling dynamics (the decay of phytoplankton blooms at depth) and changes in the character of subsurface circulation patterns –. However, low DO events in coastal areas of the Pacific Northwest are not new. Over forty years ago, Pearson and Holt  measured hypoxia (<1.5 mg L−1) in the nearshore ocean and within Grays Harbor, Washington, and Haertal et al.  documented near-hypoxic concentrations (2.2 mg L−1) in high salinity water in the Columbia River estuary. Both groups of researchers attributed these low DO events to upwelling dynamics.
Previous work in the Columbia estuary has established links between wind stress, estuarine salinity, and chlorophyll concentration , , and a strong wind-forced ocean-estuary connection has been found for many coastal estuaries in the Pacific Northwest. In Oregon these include Coos Bay , , Alsea Bay , Yaquina Bay , , and Tillamook Bay , and in Washington studies have been made in Willapa Bay , , ,  and Grays Harbor , , . Other work has revealed the influence of Columbia River outflows in delivering high concentrations of phytoplankton ,  and nutrients ,  to the estuary and nearshore ocean. These terrestrial-fluvial sources of organic matter and nutrients constitute a leading mechanism for generating oxygen stress in estuarine and coastal sites on a worldwide basis . However, DO levels in the Columbia estuary have not been routinely assessed, and it is not clear whether stressful low oxygen conditions continue to exist in the system, and, if so, from whence they are derived. In this context, note that the Columbia estuary is a critical migration and rearing habitat for endangered juvenile and adult anadromous Pacific salmon (Oncorhynchus spp.), ecologically relevant forage fishes (smelt, anchova, herring), and the economically important Dungeness crab (Cancer magister). It is not known whether low DO events in the Columbia estuary are a problem for these organisms.
Here we convey the results of field studies designed to determine the source, forcing, and resultant spatial and temporal patterns of oxygen concentration in the Columbia estuary. Specifically, we
- measured the variation in oxygen concentrations in relation to salinity to determine end-member advection versus in situ sources or sinks;
- evaluated the effects of upwelling wind and tidal forcings on patterns of estuarine oxygen concentration;
- determined the vertical and horizontal spatial extent of low DO intrusions; and
- estimated interannual variation in the number of seasonal upwelling events and the cumulative impact of low DO events among the years 2006–2008.
We then discuss possible consequences of these DO observations on migrating juvenile salmon and the life stages of Dungeness crab based on information found in the literature.
Water quality measurements
From 2006 through 2008, hydrographic measurements were made from transect (spatial survey) or anchor station (temporal survey) cruises (Figure 1). Transects included:
Circles show transect stations; triangles indicate anchor stations. The inset identifies the regional location.
- South Channel, composed of 16 stations along a 27 km transect of the Columbia River South Channel (shipping lane) extending from Buoy 10 (river kilometer (rkm) 0) to Tongue Point (rkm 27);
- North Channel, with 9 stations on a 14 km transect from Buoy 10 to the Astoria-Melger Bridge (rkm 14); and
- Mouth Line, composed of 8 stations on a 3.5 km north-south transect aligned near the mouth of the Columbia River between Clatsop Spit, OR, and Baker Bay, WA, at about rkm 5.
Observations along these three transects were made at various stages of the tide and spring/neap cycle (Table 1). Anchor stations for temporal studies were located at ∼20 m depth at station NC14, and at ∼15 m depth near stations NC07, NC10, and SC09 (Figure 1).
At each station, vertical profiles were made either with a Sea Bird Electronics (SBE) 19 plus Conductivity-Temperature-Depth (CTD) probe (2006 and 2007) or with a SBE 9/11 CTD (2008), each equipped with a SBE 43 dissolved oxygen sensor. Data were recorded at 2 Hz and binned into 0.5 m depth intervals (typically yielding >5 measurements per bin), and Surfer 8® (Golden Software) was used to interpolate salinity and oxygen profiles either spatially (transects) or temporally (anchor stations). Note that spatial interpolations were semisynoptic views biased by the speed of the research vessel. At anchor stations during 2006 and 2007, CTD casts were made at approximately 0.5 h intervals, while sampling periods were more irregular during 2008. The CTD data were used to compile oxygen-salinity (O2-S) scatterplots and to determine maximum salinity (Smax) and minimum oxygen (O2min) values.
Since the effects of low DO on migrating salmonids was of particular concern, we used literature values to categorize concentrations determined to cause biological stress in salmon , , , . Five categories of oxygen concentration were assigned:
- hypoxic or severe biological stress (0 to 2 mg L−1);
- moderate biological stress (>2 to 4 mg L−1);
- mild biological stress (>4 to 6 mg L−1);
- normoxic (>6 to ∼9 mg L−1); and
- supersaturated (>9 or 10 mg L−1).
Categories 1–3 are regarded here as low DO conditions. Note that oxygen saturation levels varied by date (based primarily on oxygen solubility in relation to temperature), and 100% saturated levels were approximately 9 mg L−1 in summer-autumn 2006 and 2007, and 10 mg L−1 in May 2007. Oxygen saturation was not determined during 2008.
Time series measurements of wind and tide
Variation in wind forcing affecting estuarine hydrology was assessed with time series of coastal wind stress. Wind velocity data was measured at the Columbia River Bar buoy (Station 46029; 46.12°N, 124.51°W; http://ndbc.noaa.gov), except during April–June 2007, when buoy loss necessitated use of data from Station 46041 (47.34°N 124.75°W). Wind vectors were converted to mean daily alongshore wind stress (τN, N m−2) from hourly observations. Positive (northward) wind stress induces downwelling and negative (southward) wind stress drives upwelling along the Pacific Northwest coast. To provide an index of the strength of wind forcing in the days prior to hydrographic sampling, we calculated time series of the 4-d cumulative mean daily wind stress (CWS). This value was based on the 1–3 d lag of the best fit cross-correlations found between wind stress and maximum daily salinity in the estuary .
Water level data was acquired from Tongue Point NOAA tide station (123.7°N, 46.2°W). Tides are a mixed semidiurnal type in the Columbia estuary. The ebb-to-flood stage of tide (SOT) during sample times was designated by assigning 0 to low water and 1.0 to high water, and partitioning the time intervals between lows and highs. Periods of flooding water were assigned positive values and periods of ebbing water were assigned negative values (e.g., 0.5 corresponds to mid-flood tide while -0.5 is mid-ebb tide). These data were used to identify semidiurnal tidal conditions during transect and anchor station sampling. The spring/neap (S/N) cycle was also set to range from 0 to 1.0, where neap periods ranged from 0.25 to 0.75 and spring periods from <0.25 to 0 and >0.75 to 1.0. The S/N cycle strongly influences circulation patterns and water column structure in the Columbia estuary , .
For each survey date, we used linear regression of oxygen-salinity (O2-S) scatterplots to evaluate the source of oxygen to the estuary, where negative slopes indicate higher oxygen concentrations in the river end-member than the ocean end-member, and positive slopes indicate the converse , , . Data from all types of transects or time series measurements were combined for each sample date.
To test for the influence of forcing functions on the distribution of estuarine water properties, we regressed daily wind (CWS) and tidal (S/N) indices with maximum daily salinity (Smax) and minimum daily oxygen (O2min) values. We also plotted the slope of individual O2-S regressions (derived above) by CWS to examine the effect of wind stress on the estuarine oxygen gradient.
The spatial scale of exposure to low DO was estimated by integrating depth-distance contour plots of DO isopleths generated from transect surveys. We used the Mouth Line transect for cross-channel and the South Channel transect for along-channel determinations (Figure 1). Cross-channel transects were made at various stages of the tide and highlight tidal-scale variation of water quality parameters. For the along-channel transects, we concentrated on samples made near slack high water to evaluate the spatial extent of low DO events. We determined area (vertical × horizontal, m2) and percent of area surveyed (total area depended on transect length) for each of the DO categories described above. Dates of the surveys are given in Table 1 along with associated tidal, wind, and hydrographic data.
As a measure of the impact of low DO events at the benthic layer, we determined the length of exposure (h) of each DO category in bottom water using time series data from anchor station studies, which we expressed as the percent of the observation period. Due to strong differences in water column stratification between spring and neap tides, we also noted the maximum vertical extent of biologically stressful water during each measurement period.
For evaluation of interannual variation during 2006–2008, we estimated the number of low DO events and the duration (d) of low DO conditions in the estuary. The period 30 March–26 November (day of year 90 through 300) was chosen to encompass the typical upwelling period in the Pacific Northwest. The number of upwelling events each year was visually assessed from time series of northward wind stress, where an event is defined as a period of at least three continuous days of τN < −0.03 N m−2 . To estimate the number of days experiencing low DO in the estuary, we applied the regression equation O2min = 6.47× (CWS) +6.0 (derived above) to the CWS time series to yield the daily minimum O2 level. We then summed the number of days for each oxygen category described above. This simple model assumes the linear relation between DO and the strength of upwelling winds would hold for values outside those measured in the field.
Of the 18 cruises made from 2006 through 2008, nine occurred during spring tide and upwelling conditions, two during spring tide and downwelling or low wind stress, three during neap tide and upwelling, and four during neap tide and downwelling (Table 1).
O2-S scatterplots were used to examine DO levels in ocean, estuarine, and river water masses during 2006–2008 (Figures 2–4). DO in the estuary was heterogeneous in space and time, due to both advection from ocean and river end-members, and also from in situ production. During the survey dates, DO ranged from supersaturated (11.7 mg L−1; 132% saturation) to near hypoxic (2.1 mg L−1; ∼30% saturation). Slopes of O2-S regressions varied among sample dates from strongly negative to near zero (Table 1). The river end-member was always normoxic (>6.0 mg L−1) and usually >90% saturated. In contrast, water imported during flood tide varied widely in both oxygen concentration and maximum salinity, with higher salinity water generally being reduced in DO. Supersaturated conditions occurred in estuarine water (3–20 psu) associated with high chlorophyll concentrations, particularly blooms of the “red water” ciliate Myrionecta rubra (see below).
A. Tidal (left axis) and spring-neap (right axis) cycles. Circles denote cruise dates. B. Bars: Low-pass filtered mean daily northward wind stress (τN, N m−2). Gray shaded sections denote upwelling events defined as ≥3 consecutive days of τN < −0.03 (dotted line). Triangles and letters indicate the timing of hydrographic cruises. C. O2-S scatterplots for designated cruises. Oxygen values are expressed as both concentration (mg L−1) and as percent saturation. Red horizontal line is the 6 mg L−1 criterion. Grey horizontal line is the 100% saturation level. Black dashed vertical line denotes upwelled water at 31 psu. Regression statistics are in Table 1.
A. Tidal and spring-neap cycles. Circles denote cruise dates. B. Bars: Low-pass filtered mean daily northward wind stress (τN, N m−2). Gray shaded sections denote upwelling events defined as ≥3 days of consecutive τN < −0.03 (dotted line). Triangles and letters indicate the timing of hydrographic cruises. C. O2-S scatterplots for designated cruises. Oxygen values are expressed as both concentration (mg L−1) and as percent saturation. Red horizontal line is the 6 mg L−1 criterion. Black dashed vertical line denotes upwelled water at 31 psu. Regression statistics are in Table 1.
A. Tidal and spring-neap cycles. Circles denote cruise dates. B. Bars: Low-pass filtered mean daily northward wind stress (τN, N m−2). Gray shaded sections denote upwelling events defined as ≥3 days of consecutive τN < −0.03 (dotted line). Triangles and letters indicate the timing of hydrographic cruises. C. O2-S scatterplots for designated cruises. Oxygen values are expressed as both concentration (mg L−1) and as percent saturation. Red horizontal line is the 6 mg L−1 criterion. Black dashed vertical line denotes upwelled water at 31 psu. Regression statistics are in Table 1.
In 2006 we made observations during late August through mid-October (Figure 2). Cruises A, B, and D were made during spring tides, C was transitional, and E was conducted during a neap tide. Cruises A–C occurred during a long period of upwelling; all O2-S regressions had negative slopes with moderate to weakly stressful DO levels in the ocean end-member. Cruises D and E occurred during downwelling conditions, regression equations had slopes near zero, and no low DO conditions were detected (concentrations at all salinities were normoxic). In 2007, we sampled in May and August (Figure 3). In May, Cruise F sampling occurred during the transition from downwelling to upwelling conditions (low wind stress), while Cruises G and H were conducted during upwelling. While all three O2-S regressions had negative slopes, only the cruises during upwelling had stressful (albeit weakly stressful) DO levels. In August we sampled during neap and spring tides. Neap tide samples (I–K) occurred during downwelling, and DO levels were supersaturated or normoxic across the salinity range. Spring tide cruises (L–N) occurred during upwelling, slopes were negative, and reduced DO levels were found in the ocean end-member. In 2008, we sampled both neap and spring tides during a protracted upwelling period (Figure 4). All O2-S regression lines were negative with levels approaching the hypoxic threshold. Thus, upwelling conditions brought various levels of oxygen-depleted water to the estuary, while during downwelling conditions estuarine, waters in the estuary were consistently normoxic or supersaturated.
Alongshore wind stress was a main driver for variation in salt and oxygen concentrations imported into the estuary. Smax was negatively related to the 4-d cumulative wind stress CWS (P = 0.014; r2 = −0.48; Figure 5A), while O2min was positively related to CWS (P<0.001; r2 = 0.81; Figure 5B). O2min was also negatively related to Smax (P<0.001; r2 = −0.51; Figure not shown). These results corroborate that during upwelling favorable periods, low DO levels occurred with high salinity water (usually >29 psu); during downwelling periods DO concentrations were usually normoxic (Figures 2–4). Additionally, the O2min-Smax regression slopes were positively related to CWS (P<0.001; r2 = 0.77; Figure 5C), indicating an increasing input of high salinity, low DO water with increasing upwelling wind stress (Table 1; Figure 5C). Conversely, slopes were weakly negative or near zero during downwelling. Neither Smax nor O2min were significantly related to the spring-neap index (P = 0.67 and 0.24, respectively). The oxygen concentration of ocean water advected into the Columbia estuary thus varied in relation to the direction and intensity of the alongshore winds.
A. Maximum salinity (Smax) by cumulative northward 4-d wind stress (CWS); B. Minimum oxygen concentration (O2min) by cumulative 4-d wind stress; C. Regression coefficients from O2min-Smax regression by cumulative 4-d wind stress. Black = 2006; blue = 2007; red = 2008.
To evaluate the vertical and horizontal spatial extent of low DO water in the Columbia estuary, we integrated depth-distance contour plots of DO isopleths generated from transect surveys. Cross-channel transects at the Mouth Line showed that large percentages of the water column were affected by low DO water (Table 2). During Cruise A, 66.3% of the water column had reduced oxygen concentrations, including 16.3% of the transect at moderate biological stress levels (Figure 6A). Note the ventilation of low DO water to the surface. Two measurements of the Mouth Line transect were made during Cruise C, the first near low tide and the second near mid-flood (Figure 6B and C). During low tide, 10.1% of the water column was supersaturated at the surface, with small pools of low DO water at depth. By the subsequent transect (mid-flood), low DO water had filled the channel from the bottom to 5–6 m below the surface (42.3% of the area) while the supersaturated zone increased in intensity but decreased in area. Cruises D and E occurred during downwelling conditions, when oxygen concentrations were normoxic or supersaturated even at salinities >31 psu (Figure 6D and E).
Salinity, top panels. Oxygen concentration, bottom panels. Plots A–C occurred during upwelling conditions, and plots D and E during downwelling conditions. Plots A, D, and E occurred near high water, while Plots B and C occurred on the same date but different stages of the tide. Salinity isopleths are 2 psu. Oxygen isopleths are 1 mg L−1, Supersaturated = blue; normoxic = white; stressed = red. Bottom contours are shown in black. Triangles designate location of measurements.
Two cruises in May 2007 were made a week apart, the first during low wind stress (Cruise F) and the second during strong upwelling conditions (Cruise G). Two measurements of the Mouth Line transect were made during each date (Figure 7). The entire water column was normoxic or supersaturated during low wind stress conditions (Figures 7A and B), while 40–45% of the water column (to 5 m) was under mild biological stress during upwelling (Figures 7C and D). Similarly, two cruises in August 2007 were made one week apart, the first during low wind stress (Cruise J) and the second during strong upwelling conditions (Cruise N), and similar results were found (Table 2). The three measurements of the Mouth Line transect that were made during Cruise N show the flushing of low DO water from the lower estuary during ebb tide (Table 2).
Salinity, top panels. Oxygen concentration, bottom panels. Plots A and B depict downwelling and C and D show upwelling conditions. For each date, two transects were made as indicated in the header. Isopleth and fill designations are as in Figure 6.
In the along-channel dimension, we sampled the South Channel transect on four dates during upwelling (Cruises A, C, H, L) and three dates during downwelling or low wind stress (Cruises D, E, I). Examples contrasting up- and downwelling conditions are shown for four surveys (A, C, D, E) in 2006 (Figure 8). These examples portray the typical salt wedge estuarine circulation observed in the Columbia estuary . Biologically stressful DO levels were found only during upwelling periods, with up to 45% of the water column affected (Table 2). Low DO in bottom waters penetrated up to 25 km in the South Channel (Figure 8C). Thus, a large area of the estuarine water column could be affected by low DO events (up to 186×103 m2 in the x-z dimension). The lowest DO values were invariably located in the highest salinity waters close to the estuary mouth.
Salinity, top panels. Oxygen concentration, bottom panels. Cruises shown in Plots A and C occurred during upwelling, while cruises in Plots B and D occurred during downwelling conditions. Isopleth and fill designations are as in Figure 6.
Nine anchor station studies were conducted to investigate the tidal-scale temporal evolution of low DO events (Table 3): Cruise B occurred near NC14 in August 2006; two pairs of observations from NC14 and NC08 were conducted under neap tide (Cruises J and K) and spring tide (Cruises M and N) conditions in August 2007; four stations near SC09 (Cruises O–Q) or NC10 (Cruise R) were observed under contrasting spring/neap tidal patterns under strong upwelling during July 2008 (Figure 1; Table 1).
In 2006 and 2007, spring tide sampling occurred during ebb-to-flood tide periods, when flooding water entered the estuary as a salt wedge. At NC14 near the estuary mouth, oxygen concentrations decreased from normoxic to <4.0 mg L−1 in a one hour period as ocean water intruded into the estuary (Figure 9A). Bottom oxygen conditions remained <6 mg L−1 for over 6.25 h (Table 3). Sampling the subsequent day at NC08, near the Astoria-Megler Bridge, revealed that low DO water was transported over 14 km upstream, where weakly stressful conditions at the bottom persisted for 3.9 h (Figure 9B, Table 3). At both stations, low DO conditions penetrated into the water column to within 5–8 m of the surface (60–70% of the water column), and Smax and O2min occurred near high water. Similarly rapid onsets of stressful conditions were observed for other spring tide measurements. In contrast, during neap tides the water column was intensely stratified, and its structure varied little during the observation periods. However these neap tide samples (Cruises J and K) occurred during downwelling conditions, and no low DO water was detected (Figures 9C and D, Table 3).
Salinity, top panels. Oxygen concentration, bottom panels. Plots A and B show upwelling during spring tides, which contrasts with Plots C and D that show downwelling during neap tides. Isopleth and fill designations are as in Figure 6.
In contrast, during 2008 there was a prolonged upwelling event during which we sampled both neap and spring tidal conditions. Moderately stressful to nearly hypoxic water was present in high salinity water during all four dates (Figure 10). During spring tides on 18 and 20 July, the water column structure again followed a salt wedge pattern as described above. Exposure to low DO occurred only when salinity exceeded 25–29 psu. At high tide, low DO water penetrated to within 2 m of the surface on 20 July and outcropped during 18 July (Figures 10A and B). Exposure to low DO conditions at the estuary benthic layer ranged from 26.4 to 60.8% of the measurement period (Table 3). In contrast, during the neap period of high stratification, moderately stressful to nearly hypoxic water was present in bottom water throughout the measurement periods (100% exposure), which were for 8 hours on 10 July and 4.5 h on 13 July (Figures 10C and D, Table 3). Mildly to moderately stressful levels were present within 5–6 m of the surface at high water, and encompassed 56.8 and 59.1%, respectively, of the space-time periods measured. These data show low DO water was associated with high salinity water, was maximal in vertical extent around high tide, and persisted or was advected in accordance with semidiurnal tidal patterns.
Salinity, top panels. Oxygen concentration, bottom panels. The plots contrast spring tides (A and B) from neap tides (C and D) during a strong upwelling event. Isopleth and fill designations are as in Figure 6.
The annual number of upwelling events and the number of days per year estimated to have reduced DO in the estuary varied among years (Table 4). Based on the 4-d cumulative wind stress time series, there ranged an almost two-fold difference (6 and 11) in the number of low DO events between 2006 and 2008. The total number of days estimated to have DO <6 mg L−1 ranged from 103 to 152 (49 to 72% of the periods evaluated). Based on wind stress intensity, periods of severe low were rare, while periods of moderate DO stress ranged from 13 to 23% of the upwelling period. There was no relation between the number of low DO events and total number of days with stressful conditions, since the duration of the wind events varied. Thus, based on wind stress records, low DO events are likely to be common in the Columbia estuary.
Origins of low DO water
Low DO occurs naturally in subsurface waters of the California Current System, but the origin of this source water can be from either the north or south of the Columbia estuary depending on the influence of large-scale climatic factors on the North Pacific Gyre . Waters upwelled on the shelf appear to come primarily from the northward-flowing California Current Undercurrent at depths of 150–300 m. Feely et al.  found water from a depth of 150 m was upwelled to the surface from about 40 km offshore to the nearshore zone during strong upwelling. In addition to being oxygen-depleted, this water was also undersaturated with respect to aragonite and was therefore acidic to calcified organisms. In contrast, Wheeler et al.  and Grantham et al.  concluded the hypoxic mortalities that occurred on the Oregon shelf in 2002 were due to a combination of low DO source waters plus the oxidation of organic matter originating from the decline of a large diatom bloom that sank and was respired in the benthic bottom layer. In that case, the source waters were determined to be from an anomalous southward transport of subarctic water which was unusually high in nitrate and low in DO , . Kaplan et al.  found interannual variation in the timing and intensity of upwelling led to variation in the source of upwelled water off Central California between 2006 and 2007. It appears both physical advection and biological processes affect the character of water intruding on the shelf, which then becomes the source water for upwelling, and several recent studies have documented low DO water on the Oregon shelf in proximity to estuarine systems , –, . Processes that supply oxygen-depleted water to the nearshore zone, whether the mechanism be variation in along-shelf advection, wind-induced changes in upwelling intensity, in situ depletion due to heterotrophic respiration, or some combination of these factors, would all contribute to a nearshore pool of low DO source water that can be advected into Pacific Northwest estuaries.
We sampled the distribution of DO in the Columbia estuary on 18 cruises that spanned a range of both salinities and of upwelling- and downwelling-favorable wind stresses. The results clearly show that low DO water was invariably associated with the ocean end-member, while the river end-member was consistently normoxic. Further, low DO events occurred during upwelling wind events, and when downwelling winds predominated, the water of maximum salinity was generally normoxic. Based on O2min, the intensity of low DO events was positively related to the strength of upwelling winds, indicating greater upwelling results in lower DO in the estuary. Transitions between up- and downwelling conditions, and the delivery of low DO water to the estuary, varied rapidly over the course of a few days. Our findings confirm the origin of low DO water in the Columbia estuary was upwelled subsurface water advected into the estuary from the ocean, and corroborate findings from the 1950s and 1960s as reported by Pearson and Holt  and Haertal et al. .
The distribution, duration, and extent of low DO events varied temporally on semidiurnal tidal and spring/neap tidal scales which, along with streamflow, determine estuarine circulation patterns in the CRE. The density structure of the estuary modulates from a mainly vertically mixed, horizontally stratified (salt wedge) system during spring tides to a highly stratified state during neap tides , . During spring tides, the estuary was well flushed on semidiurnal time scales, and high salinity, low DO water that intruded during flood tides was replaced by normoxic river water during the subsequent ebb flow (Figures 6B,7A). Exposure times of biologically stressful levels of oxygen to organisms during these periods were limited to a maximum of about 6 h near the estuary mouth and 4 h upstream near station NC14 (Table 2); however, the vertical extent of low DO was greatest during spring tides and could even outcrop to the surface (Figures 6A and 10A). During neap tides, estuarine waters were highly stratified, flushing was reduced, and high salinity bottom water had increased residence in the estuary (Table 3). For example, during the strong upwelling event in July 2008 (Figure 9), the neap tide series caused a much longer exposure of low DO to benthic organisms than during the following spring tide series when flushing was increased (100% exposure versus 36% for neap versus spring tide sampling periods of similar length). Stressful conditions at the benthic layer were maximized when strong upwelling occurred around neap tides. In contrast, the greatest vertical affect was found during spring tides at sections near the mouth of the estuary, when the entire water column could be rendered stressful. Together, time series and transect data indicated that large expanses of the water column and benthic layer were exposed to low DO water.
Autochthonous oxygen production in the CRE
Despite the highly advective nature of the Columbia estuary , biological activity by phototrophic organisms was a source of oxygen within the estuary. Surface waters were frequently supersaturated in water of mesohaline salinity (Figures 2–4, Cruises C–E, I–L). This indicates an autochthonous estuarine source of oxygen. During summer and early autumn, the chlorophyll signal in the Columbia estuary is usually dominated by the highly motile mixotrophic ciliate Myrionecta rubra, which forms dense “red water” blooms , . The distribution of M. rubra was spatially coincident with high oxygen concentrations during August and September  and usually occurred at salinities between 3 and 20 psu. The highest vertical oxygen gradients (−1.3 mg L−1 m−1) were found in shallow water during autumn, when low DO ocean water intruded under this estuarine-produced supersaturated surface waters (Figure 6C). However, the biological impact of biota was also found during May 2006, when 38% of the water column was supersaturated along the Mouth Line transect (Figure 7A–B). This production was likely due to riverine diatoms . Wheeler et al.  found supersaturated surface conditions within 10 km of the Oregon coast during July 2002, but this occurred in salinities >33 psu and is indicative of production by coastal phytoplankton. At present, it is not well determined how oxygen production by phytoplankton may alleviate low DO in upwelled water; however the same upwelled water that is low in DO is high in nitrate and therefore is stimulatory for phytoplankton growth. The normoxic oxygen levels observed in the ocean end-member during downwelling conditions may in part be due to oxygen production by coastal phytoplankton and the subsequent transport of those water masses to the estuary .
Potential effects of low DO on salmon and crab
Each year during the upwelling season, around 100 million juvenile Pacific salmon migrate through the Columbia estuary to the ocean. There are no field measurements to discern the impacts of low DO on these salmon; however, information from the literature suggests there are effects and interactions that would reduce fitness and/or increase predation. These include avoidance behavior and subsequent habitat constriction, impaired swimming ability, and reduced feeding and growth . Studies have demonstrated that salmon are relatively intolerant to low DO and usually exhibit avoidance behaviors when exposed to reduced oxygen levels. A review by Davis  concluded the average minimum incipient response threshold for salmonids in freshwater was 6.0 mg L−1, while the US Environmental Protection Agency (EPA)  rated 3.0 mg L−1 as the limit to avoid acute mortality. Whitmore et al.  found juvenile Chinook (O. tshawytscha) and coho (O. kisutch) salmon avoided water <4.5 and 6.0 mg L−1, respectively, and both species preferred concentrations >9.0 mg L−1. Birtwell and Kruzynski  found that juvenile Chinook salmon avoided low DO bottom water in the highly stratified Somass River estuary, BC, Canada, and, by this avoidance behavior, the salmon became isolated in unsuitably warm and polluted surface areas with reduced prey resources. In laboratory experiments, these authors found surface-oriented Chinook salmon were induced to descend into saline water when oxygen concentrations in the surface layer were decreased from 9 to between 7 and 8 mg L−1. It should be noted that returning adult salmon also avoid water with oxygen concentrations below about 3.5 mg L−1 , . Many other fish and invertebrate species undergo vertical and horizontal habitat displacements to avoid intruding low DO bottom water (e.g., , , ).
Migrating salmon have been shown to exhibit a subsurface preference –, and a vertical range restriction could have profound impacts on salmon migrating through the Columbia estuary. This is due to the high densities of piscivorous birds such as Caspian terns (Hydroprogne caspia) that nest and roost on East Sand Island in the lower estuary . Price and Schreck  and Kennedy et al.  suggest avoidance of high salinity water due to stress or maladaptation of osmoregulation may concentrate migrating fish to low salinity surface layers, where they maybe more vulnerable to predation by shallow-feeding plunge-divers. An avoidance response to low DO in intruding ocean water could similarly increase predation rates on salmon by these birds. DO levels during our study were commonly <6.0 mg L−1 within 5 m of the surface and low DO water occasionally outcropped at the surface at levels that likely induced a behavioral response by salmon. Moreover, low DO progressively reduces swimming speed in juvenile salmon (by approximately 20% at 4.0 mg L−1 –, with the consequence that escape responses to diving birds such as double-crested cormorants (Phalacrocorax auritus) or predatory fishes could be impeded. Note that the two bird species mentioned here are estimated to consume millions of migrating salmon annually , . We speculate periods of shoaling low DO water in the Columbia estuary may lead to increased predation rates by birds on salmon as well as on other small pelagic fishes.
Salmon likely suffer additional non-lethal effects to low DO exposure. Summarizing a series of growth experiments with juvenile Chinook and coho salmon in freshwater, the U.S. EPA  reported exponential decreases in median growth from a minimal effect at 7.0 mg L−1 to a decrease of 42±7.1% at 3.0 mg L−1. Growth reductions for salmon exposed to DO levels below 4.0 mg L−1 were considered to be severe. The critical criterion for growth of saltwater organisms was determined to be 4.8 mg L−1 . The mechanism for growth reductions with increasing oxygen stress appears to be a combination of enhanced metabolic demand and decreased feeding. Moreover, stress has been found to increase predation rates on juvenile salmonids , , which suggests that salmon metabolically weakened or stressed by low DO events may be more susceptible to predators. Low DO in surface waters on the shelf may also affect salmon once they migrate from the estuary [e.g., 46]. Thus, while DO levels in the Columbia estuary are unlikely to be directly lethal to salmonids, behavioral and physiological responses to low DO that reduce performance and increase stress may increase predation risk and/or decrease fitness of migrating fish. More research is required to elucidate behavioral and sublethal effects of low DO on salmon.
Pacific Northwest estuaries such as the Columbia are also important nursery areas for Dungeness crabs , and benthic fauna with limited mobility are often considered more susceptible to low DO events than mobile nekton. Shelf anoxia in 2002 led to widespread mortality of benthic organisms, including Dungeness crab , but crabs are also affected by non-lethal oxygen concentrations. Bernatis et al.  determined Dungeness crabs to be relatively intolerant of DO levels <47% saturation (which is more tolerant than most crustaceans, ), and Stone and O'Clair  similarly found adult crabs in Barkley Sound avoided water <50% saturation. Crabs reduce their food intake in hypoxia, and while they may forage in low DO areas, they tend to move to areas of higher DO concentration for digestion (which consumes oxygen). One point of concern regards the cumulative effects of low DO and salinity on Dungeness crab biology in the Columbia estuary. Cancer magister is a weak osmoregulator and becomes inactive at reduced salinities . Sugerman et al.  found crabs reduce pumping water over the gills to curtail ionic loss at 23 psu, and cease pumping at 16 psu. Curtis et al.  found crabs reduced both overall feeding activity and the quantity of food ingested at mesohaline salinities. Salinity levels in the Columbia estuary commonly fall below 16 psu during ebbing tides (e.g., Figures 7, 10), at which time crabs are probably quiescent. If activity during subsequent flood tide is also limited due to low DO, then the time available for crab foraging could be reduced, as was found for blue crab (Callinectes sapidus) by Seitz et al. . Further uncertainties include the effects of low DO on settlement and survival of C. magister megalopae (the recruiting larval form), which usually enter Pacific Northwest estuaries from April through November . For megalopae of the Atlantic rock crab (C. irroratus), the median lethal concentration (LC50) values during 240 min tests ranged from 1.2 mg L−1 at 10°C to 3.3 mg L−1 at 30°C , which suggests larval crab could be affected by DO values we recorded in the Columbia estuary. It is not known if low DO affects metamorphic success of larval Dungeness crab.
Potential effects of climate change
Although low DO in the coastal Pacific Northwest is not a new phenomenon , , long-term trends indicate the frequency and severity of low DO events may be increasing due to climatic alterations in atmospheric forcings and changes in ocean circulation patterns , . The depth of the oxygen minimum zone in the California Current System has been shoaling , –, and this is the source water for coastal upwelling on the Pacific Northwest continental shelf. Modeling predicts further declines in DO are likely to occur, based on increased isolation of bottom waters by strengthened thermal stratification and reduced vertical mixing . However, the most recent review of coastal estuaries in the Pacific Northwest failed to identify low DO as problematic , and the impact of low DO on organisms in the Columbia estuary and other PNW estuaries has not been ascertained. Based on a wind-forced supply mechanism, low DO events in the Columbia estuary appear to be common at present (Table 4), and along with increased acidification of this subsurface water , , shelf and estuarine habitats could be experiencing declines in environmental quality.
1. Low DO water was advected into the Columbia River estuary from the ocean end-member; the riverine end-member was always normoxic.
2. Oxygen depleted water in the estuary was associated with upwelling wind events, and low DO was not detected during periods of downwelling or low wind stress.
3. Spring-neap tidal stratification largely determined levels of exposure to low DO water, with greater vertical extent during spring tides and greater horizontal and benthic impacts during neap tides.
4. Hypoxic oxygen concentrations were not measured during our sampling; however, DO levels were sufficiently low to affect the behavior of migrating juvenile salmon and benthic crabs (according to literature values).
We appreciate the efforts of Captains Gene Bock (2006) and Tim Stentz (2007), crew, and students working on R/V Forerunner, and thank Captain Ray McQuin, crew, and participants aboard the UNOLS vessel R/V Clifford Barnes (2008). Thanks are given to Julie Scheurer (NOAA), Fred Prahl (Oregon State University), and two anonymous referees for helpful reviews. Reference to trade names does not imply endorsement by NOAA or the Oregon Graduate Institute.
Conceived and designed the experiments: GCR JAN AMB. Performed the experiments: GCR JAN. Analyzed the data: GCR JAN AMB. Contributed reagents/materials/analysis tools: GCR JAN AMB. Wrote the paper: GCR JAN AMB.
- 1. Diaz RJ, Rosenberg R (2008) Spreading dead zones and consequences for marine ecosystems. Science 321: 926–929.RJ DiazR. Rosenberg2008Spreading dead zones and consequences for marine ecosystems.Science321926929
- 2. Diaz , RJ , Breitburg DL (2009) The hypoxic environment. In: Richards JG, Farrell AP, Brauner CJ, editors. Hypoxia. Fish Physiology Vol 27. Amsterdam: Academic Press. pp 2–23: DiazRJDL Breitburg2009The hypoxic environment. In: Richards JG, Farrell AP, Brauner CJ, editors. Hypoxia. Fish Physiology Vol 27. Amsterdam: Academic Press.pp2–23
- 3. Breitburg DL, Hondorp L, Davis W, Diaz RJ (2009) Hypoxia, nitrogen and fisheries: Integrating effects across local and global landscapes. Ann Rev Mar Sci 1: 329–350.DL BreitburgL. HondorpW. DavisRJ Diaz2009Hypoxia, nitrogen and fisheries: Integrating effects across local and global landscapes.Ann Rev Mar Sci1329350
- 4. Rabalais NN, Turner RE, Wiseman WJ (2002) Gulf of Mexico hypoxia, aka The Dead Zone. Ann Rev Ecol Sys 33: 235–263.NN RabalaisRE TurnerWJ Wiseman2002Gulf of Mexico hypoxia, aka The Dead Zone.Ann Rev Ecol Sys33235263
- 5. Helly JJ, Levin LA (2004) Global distribution of naturally occurring marine hypoxia on continental margins. Deep-sea Res I 51: 1159–1168.JJ HellyLA Levin2004Global distribution of naturally occurring marine hypoxia on continental margins.Deep-sea Res I5111591168
- 6. Paulmier A, Ruiz-Pino D (2008) Oxygen Minimum Zones (OMZs) in the modern ocean. Prog Oceanogr. A. PaulmierD. Ruiz-Pino2008Oxygen Minimum Zones (OMZs) in the modern ocean.Prog Oceanogr
- 7. Hales B, Karp-Boss L, Perlin A, Wheeler PA (2006) Oxygen production and carbon sequestration in an upwelling margin. Global Biogeol Cycles 20, GB3001.B. HalesL. Karp-BossA. PerlinPA Wheeler2006Oxygen production and carbon sequestration in an upwelling margin.Global Biogeol Cycles20, GB3001
- 8. Takahashi T, Nakata H, Hirano K, Matsuoka K, Iwataki M, et al. (2009) Upwelling of oxygen-depleted water (sumishio) in Omura Bay, Japan J Oceanogr 65: 113–120.T. TakahashiH. NakataK. HiranoK. MatsuokaM. Iwataki2009Upwelling of oxygen-depleted water (sumishio) in Omura Bay, Japan J Oceanogr65113120
- 9. Tyler RM, Targett TE (2007) Juvenile weakfish Cynoscion regalis distribution in relation to diel-cycling dissolved oxygen in an estuarine tributary. Mar Ecol Prog Ser 333: 257–269.RM TylerTE Targett2007Juvenile weakfish Cynoscion regalis distribution in relation to diel-cycling dissolved oxygen in an estuarine tributary.Mar Ecol Prog Ser333257269
- 10. Nezlin NP, Kamer K, Hyde J, Stein ED (2009) Dissolved oxygen dynamics in a eutrophic estuary, Upper Newport Bay, California. Est Coast Shelf Sci 82: 139–151.NP NezlinK. KamerJ. HydeED Stein2009Dissolved oxygen dynamics in a eutrophic estuary, Upper Newport Bay, California.Est Coast Shelf Sci82139151
- 11. Davis JC (1975) Minimal dissolved oxygen requirements of aquatic life with emphasis on Canadian species: a review. J Fish Res Bd Canada 32: 2295–2332.JC Davis1975Minimal dissolved oxygen requirements of aquatic life with emphasis on Canadian species: a review.J Fish Res Bd Canada3222952332
- 12. Breitburg , DL , Loher T, Pacey CA, Gerstein A (1997) Varying effects of low dissolved oxygen on trophic interactions in an estuarine food web. Ecol Monogr 67: 489–507.BreitburgDLT. LoherCA PaceyA. Gerstein1997Varying effects of low dissolved oxygen on trophic interactions in an estuarine food web.Ecol Monogr67489507
- 13. Vaquer-Sunyer R, Duarte CM (2008) Thresholds of hypoxia for marine biodiversity. Proc Natl Acad Sci 105: 15452–15457.R. Vaquer-SunyerCM Duarte2008Thresholds of hypoxia for marine biodiversity.Proc Natl Acad Sci1051545215457
- 14. Environmental Protection Agency (1986) Ambient water quality criteria for dissolved oxygen. EPA 440/5-86-003. Environmental Protection Agency1986Ambient water quality criteria for dissolved oxygen.EPA 440/5-86-003
- 15. Kramer DL (1987) Dissolved oxygen and fish behavior. Environ Biol Fish 18: 81–92.DL Kramer1987Dissolved oxygen and fish behavior.Environ Biol Fish188192
- 16. Bricker SB, Ferrieira JG, Simas T (2003) An integrated methodology for assessment of estuarine trophic status. Ecol Model 169: 39–60.SB BrickerJG FerrieiraT. Simas2003An integrated methodology for assessment of estuarine trophic status.Ecol Model1693960
- 17. Huyer A (1983) Coastal upwelling in the California Current System. Prog Oceanogr 12: 259–284.A. Huyer1983Coastal upwelling in the California Current System.Prog Oceanogr12259284
- 18. Hickey BM (1989) Patterns and processes of circulation over the shelf and slope. In: Hickey BM, Landry MR, editors. Coastal oceanography of Washington and Oregon. New York: Elsevier. pp. 41–115.BM Hickey1989Patterns and processes of circulation over the shelf and slope.BM HickeyMR LandryCoastal oceanography of Washington and OregonNew YorkElsevier41115
- 19. Roegner GC, Hickey B, Newton J, Shanks A, Armstrong D (2002) Wind-induced plume and bloom intrusions into Willapa Bay, Washington. Limnol Oceanogr 47: 1033–1042.GC RoegnerB. HickeyJ. NewtonA. ShanksD. Armstrong2002Wind-induced plume and bloom intrusions into Willapa Bay, Washington.Limnol Oceanogr4710331042
- 20. Wheeler PA, Huyer A, Fleischbein J (2003) Cold halocline, increased nutrients and higher chlorophyll off Oregon in 2002. Geophys Res Let 30, 8021.PA WheelerA. HuyerJ. Fleischbein2003Cold halocline, increased nutrients and higher chlorophyll off Oregon in 2002.Geophys Res Let30, 8021
- 21. Chan F, Barth JA, Lubchenco J, Kirincich A, Weeks H, et al. (2008) Emergence of anoxia in the California Current Large Marine Ecosystem. Science 319: 920.F. ChanJA BarthJ. LubchencoA. KirincichH. Weeks2008Emergence of anoxia in the California Current Large Marine Ecosystem.Science319920
- 22. Grantham B, Chan F, Nielsen KJ, Fox DS, Barth JA, et al. (2004) Upwelling-driven nearshore hypoxia signals ecosystem and oceanographic changes in the northeast Pacific. Nature 429: 749–754.B. GranthamF. ChanKJ NielsenDS FoxJA Barth2004Upwelling-driven nearshore hypoxia signals ecosystem and oceanographic changes in the northeast Pacific.Nature429749754
- 23. Deutsch C, Emerson S, Thompson L (2005) Fingerprints of climate change in North Pacific oxygen. Geophys Res Let 32: L16604.C. DeutschS. EmersonL. Thompson2005Fingerprints of climate change in North Pacific oxygen.Geophys Res Let32L16604
- 24. Pearson EA, Holt GA (1960) Water quality and upwelling at Grays Harbor entrance. Limnol Oceanogr 5: 48–56.EA PearsonGA Holt1960Water quality and upwelling at Grays Harbor entrance.Limnol Oceanogr54856
- 25. Haertel L, Osterberg C, Curl H Jr, Park PK (1969) Nutrient and plankton ecology of the Columbia River estuary. Ecology 50: 962–978.L. HaertelC. OsterbergH. Curl JrPK Park1969Nutrient and plankton ecology of the Columbia River estuary.Ecology50962978
- 26. Roegner GC, Seaton C, Baptista A (2010) Tidal and climatic forcing of hydrography and chlorophyll patterns in the Columbia River estuary. Estuar Coasts. GC RoegnerC. SeatonA. Baptista2010Tidal and climatic forcing of hydrography and chlorophyll patterns in the Columbia River estuary.Estuar Coasts
- 27. Roegner GC, Shanks A (2001) Import of coastally-derived chlorophyll a to South Slough, Oregon. Estuaries 24: 244–256.GC RoegnerA. Shanks2001Import of coastally-derived chlorophyll a to South Slough, Oregon.Estuaries24244256
- 28. Hickey BM, Banas NS (2003) Oceanography of the US Pacific Northwest coastal ocean and estuaries with application to coastal ecology. Estuaries 26: 1010–1031.BM HickeyNS Banas2003Oceanography of the US Pacific Northwest coastal ocean and estuaries with application to coastal ecology.Estuaries2610101031
- 29. de Angelis MA, Gordon LI (1985) Upwelling and river runoff as sources of dissolved nitrous oxide to the Aslea Estuary, Oregon. Estuar Coast Shelf Sci 20: 375–386.MA de AngelisLI Gordon1985Upwelling and river runoff as sources of dissolved nitrous oxide to the Aslea Estuary, Oregon.Estuar Coast Shelf Sci20375386
- 30. Sigleo AC Mordy CW, Stabeno P, Frick WE (2005) Nitrate variability along the Oregon coast: Estuarine-coastal exchange. Estuar Coast Shelf Sci 64: 211–222.CW Sigleo AC MordyP. StabenoWE Frick2005Nitrate variability along the Oregon coast: Estuarine-coastal exchange.Estuar Coast Shelf Sci64211222
- 31. Brown CA, Ozretich RJ (2009) Coupling between the coastal ocean and Yaquina Bay, Oregon: Importance of oceanic inputs relative to other nitrogen sources. Estuar Coasts 23: 219–237.CA BrownRJ Ozretich2009Coupling between the coastal ocean and Yaquina Bay, Oregon: Importance of oceanic inputs relative to other nitrogen sources.Estuar Coasts23219237
- 32. Colbert D, McManus J (2003) Nutrient biogeochemistry in an upwelling-influenced estuary of the Pacific Northwest (Tillamook Bay, Oregon, USA) Estuaries 26: 1205–1219.D. ColbertJ. McManus2003Nutrient biogeochemistry in an upwelling-influenced estuary of the Pacific Northwest (Tillamook Bay, Oregon, USA) Estuaries2612051219
- 33. Roegner GC, Armstrong D, Hickey B, Shanks A (2003) Ocean distribution of Dungeness crab megalopae and recruitment patterns to estuaries in southern Washington State. Estuaries 26: 1058–1070.GC RoegnerD. ArmstrongB. HickeyA. Shanks2003Ocean distribution of Dungeness crab megalopae and recruitment patterns to estuaries in southern Washington State.Estuaries2610581070
- 34. Banas NS, Hickey , BM , Newton , JA , Ruesink , JL (2007) Tidal exchange, bivalve grazing, and patterns of primary production in Willapa Bay, Washington, USA. Mar Ecol Prog Ser 341: 123–139.NS BanasHickeyBMNewtonJARuesinkJL2007Tidal exchange, bivalve grazing, and patterns of primary production in Willapa Bay, Washington, USA.Mar Ecol Prog Ser341123139
- 35. Sullivan BA, Prahl FG, Small LF, Covert PA (2001) Seasonality of phytoplankton production in the Columbia River: A natural or anthropogenic pattern? Geochimica et Cosmochimica Acta 65: 1125–1139.BA SullivanFG PrahlLF SmallPA Covert2001Seasonality of phytoplankton production in the Columbia River: A natural or anthropogenic pattern?Geochimica et Cosmochimica Acta6511251139
- 36. Prahl , FG , Small LF, Sullivan BA, Cordell J, Simenstad CA, et al. (1998) Biogeochemical gradients in the lower Columbia River. Hydrobiologia 361: 37–52.PrahlFGLF SmallBA SullivanJ. CordellCA Simenstad1998Biogeochemical gradients in the lower Columbia River.Hydrobiologia3613752
- 37. Bruland KW, Lohan MC, Aguilar-Islas AM, Smith GJ, Sohst B, et al. (2008) Factors influencing the chemistry of the near-field Columbia River plume: Nitrate, silicic acid, dissolved Fe, and dissolved Mn. J Geophys Res 113, C00B02.KW BrulandMC LohanAM Aguilar-IslasGJ SmithB. Sohst2008Factors influencing the chemistry of the near-field Columbia River plume: Nitrate, silicic acid, dissolved Fe, and dissolved Mn.J Geophys Res113, C00B02
- 38. Environmental Protection Agency (2000) Ambient aquatic life water quality criteria for dissolved oxygen (saltwater): Cape Cod to Cape Hatteras. Environmental Protection Agency2000Ambient aquatic life water quality criteria for dissolved oxygen (saltwater): Cape Cod to Cape HatterasEPA-822-R-00-012. EPA-822-R-00-012.
- 39. Washington State Department of Ecology (2006) Water quality standards for surface waters of the State of Washington.Washington State Department of Ecology2006Water quality standards for surface waters of the State of Washington.Publication Number 06-10-091 Available online: http://www.ecy.wa.gov/biblio/0610091.html. Accessed 2010 June 21. Publication Number 06-10-091 Available online: http://www.ecy.wa.gov/biblio/0610091.html. Accessed 2010 June 21.
- 40. Jay DA, Smith JD (1990) Circulation, density distribution, and neap-spring transitions in the Columbia River Estuary. Progr Oceanogr 25: 81–112.DA JayJD Smith1990Circulation, density distribution, and neap-spring transitions in the Columbia River Estuary.Progr Oceanogr2581112
- 41. Di Lorenzo E, Schneider N, Cobb KM, Franks PJS, Chhak K et al (2008) North Pacific Gyre Oscillation links ocean climate and ecosystem change. Geophys Res Let 35: L08607.E. Di LorenzoN. SchneiderKM CobbPJS Franksal Chhak K et2008North Pacific Gyre Oscillation links ocean climate and ecosystem change.Geophys Res Let35L08607
- 42. Feely RA, Sabine CL, Hernandez-Ayon JM, Ianson D, Hales B (2008) Evidence for upwelling of corrosive “acidified” water onto the continental shelf. Science 320: 1490–1492.RA FeelyCL SabineJM Hernandez-AyonD. IansonB. Hales2008Evidence for upwelling of corrosive “acidified” water onto the continental shelf.Science32014901492
- 43. Freeland HJ, Gatien G, Huyer A, Smith RL (2003) Cold halocline in the northern California Current: An invasion of subarctic water. Geophys Res Let 30: 1141.HJ FreelandG. GatienA. HuyerRL Smith2003Cold halocline in the northern California Current: An invasion of subarctic water.Geophys Res Let301141
- 44. Kaplan DM, Halle C, Paduan J, Largier JL (2009) Surface currents during anomalous upwelling seasons off central California. J Geophys Res-Oceans 114: C12026.DM KaplanC. HalleJ. PaduanJL Largier2009Surface currents during anomalous upwelling seasons off central California.J Geophys Res-Oceans114C12026
- 45. Lohan MC, Bruland KW (2008) Elevated Fe(III) and dissolved Fe in hypoxic shelf waters off Oregon and Washington: An enhanced source of iron to coastal upwelling regimes. Environ Sci Tech 42: 6462–6468.MC LohanKW Bruland2008Elevated Fe(III) and dissolved Fe in hypoxic shelf waters off Oregon and Washington: An enhanced source of iron to coastal upwelling regimes.Environ Sci Tech4264626468
- 46. Herfort L, Peterson , TD , McCue LA, Crump BC, Prahl FG, et al. (2011) Myrionecta rubra population genetic diversity and its cryptophyte chloroplast specificity in recurrent red tides in the Columbia River estuary. Aquat Microb Ecol 62: 85–97.L. HerfortPetersonTDLA McCueBC CrumpFG Prahl2011Myrionecta rubra population genetic diversity and its cryptophyte chloroplast specificity in recurrent red tides in the Columbia River estuary.Aquat Microb Ecol628597
- 47. Whitmore CM, Warren CE, Doudoroff P (1960) Avoidance reactions of salmonid and centrarchid fishes to low oxygen concentrations. Trans Am Fish Soc 89: 17–26.CM WhitmoreCE WarrenP. Doudoroff1960Avoidance reactions of salmonid and centrarchid fishes to low oxygen concentrations.Trans Am Fish Soc891726
- 48. Birtwell IK, Kruzynski GM (1989) In situ and laboratory studies on the behaviour and survival of Pacific salmon (genus Oncorhynchus) Hydrobiologia 188/ 189: 543–560.IK BirtwellGM Kruzynski1989In situ and laboratory studies on the behaviour and survival of Pacific salmon (genus Oncorhynchus) Hydrobiologia 188/189543560
- 49. Alabaster JS (1988) The dissolved-oxygen requirements of upstream migrant chinook salmon, Oncorhynchus tshawytscha, in the lower Willamette River, Oregon. J Fish Biol 32: 635–636.JS Alabaster1988The dissolved-oxygen requirements of upstream migrant chinook salmon, Oncorhynchus tshawytscha, in the lower Willamette River, Oregon.J Fish Biol32635636
- 50. Birtwell IK (1989) Comments on the sensitivity of salmonids to reduced levels of dissolved oxygen and to pulp mill pollution in Neroutsos Inlet, British Columbia. Can Tech Rep Fish Aquat Sci 1695: 27.IK Birtwell1989Comments on the sensitivity of salmonids to reduced levels of dissolved oxygen and to pulp mill pollution in Neroutsos Inlet, British Columbia.Can Tech Rep Fish Aquat Sci169527
- 51. Hazen EL, Craig JK, Good CP, Crowder LB (2009) Vertical distribution of fish biomass in hypoxic waters on the Gulf of Mexico shelf. Mar Ecol Prog Ser 375: 195–207.EL HazenJK CraigCP GoodLB Crowder2009Vertical distribution of fish biomass in hypoxic waters on the Gulf of Mexico shelf.Mar Ecol Prog Ser375195207
- 52. Ludsin SA, Zhang X, Brandt SB, Roman MR, Boicourt WC, et al. (2009) Hypoxia-avoidance by planktivorous fish in Chesapeake Bay: Implications for food web interactions and fish recruitment. J Exp Mar Biol Ecol 381: S121–131.SA LudsinX. ZhangSB BrandtMR RomanWC Boicourt2009Hypoxia-avoidance by planktivorous fish in Chesapeake Bay: Implications for food web interactions and fish recruitment.J Exp Mar Biol Ecol381S121131
- 53. Dauble DD, Page TL, Hanf RW Jr (1989) Spatial distribution of juvenile salmonids in the Hanford Reach, Columbia River. Fish Bull 87: 775–790.DD DaubleTL PageRW Hanf Jr1989Spatial distribution of juvenile salmonids in the Hanford Reach, Columbia River.Fish Bull87775790
- 54. Beeman JW, Maule AG (2006) Migration depths of juvenile Chinook salmon and steelhead relative to total dissolved gas supersaturation in a Columbia River reservoir. Trans Am Fish Soc 135: 584–594.JW BeemanAG Maule2006Migration depths of juvenile Chinook salmon and steelhead relative to total dissolved gas supersaturation in a Columbia River reservoir.Trans Am Fish Soc135584594
- 55. Webster SJ, Dill LM, Korstrom JS (2007) The effects of depth and salinity on juvenile Chinook salmon Oncorhynchus tshawytscha (Walbaum) habitat choice in an artificial estuary. J Fish Biol 71: 842–851.SJ WebsterLM DillJS Korstrom2007The effects of depth and salinity on juvenile Chinook salmon Oncorhynchus tshawytscha (Walbaum) habitat choice in an artificial estuary.J Fish Biol71842851
- 56. Collis K, Roby DD, Craig DP, Ryan BA, Ledgerwood RD (2001) Colonial waterbird predation on juvenile salmonids tagged with passive integrated transponders in the Columbia River estuary: Vulnerability of different salmonid species, stocks, and rearing types. Trans Am Fish Soc 130: 385–396.K. CollisDD RobyDP CraigBA RyanRD Ledgerwood2001Colonial waterbird predation on juvenile salmonids tagged with passive integrated transponders in the Columbia River estuary: Vulnerability of different salmonid species, stocks, and rearing types.Trans Am Fish Soc130385396
- 57. Price CS, Schreck CB (2003) Stress and saltwater-entry behavior of juvenile chinook salmon (Oncorhynchus tshawytscha): conflicts in physiological motivation. Can J Fish Aquat Sci 60: 910–918.CS PriceCB Schreck2003Stress and saltwater-entry behavior of juvenile chinook salmon (Oncorhynchus tshawytscha): conflicts in physiological motivation.Can J Fish Aquat Sci60910918
- 58. Kennedy BM, Gale WL, Ostrand KG (2007) Relationship between smolt gill Na+, K+ ATPase activity and migration timing to avian predation risk of steelhead trout (Oncorhynchus mykiss) in a large estuary. Can J Fish Aquat Sci 64: 1506–1516.BM KennedyWL GaleKG Ostrand2007Relationship between smolt gill Na+, K+ ATPase activity and migration timing to avian predation risk of steelhead trout (Oncorhynchus mykiss) in a large estuary.Can J Fish Aquat Sci6415061516
- 59. Davis GE, Foster J, Warren CE, Doudoroff P (1963) The influence of oxygen concentration on the swimming performance of juvenile Pacific salmon at various temperatures. Trans Amer Fish Soc 92: 111–124.GE DavisJ. FosterCE WarrenP. Doudoroff1963The influence of oxygen concentration on the swimming performance of juvenile Pacific salmon at various temperatures.Trans Amer Fish Soc92111124
- 60. Dahlberg ML, Shumway DL, Doudorof , P (1968) Influence of dissolved oxygen and carbon dioxide on swimming performance of largemouth bass and coho salmon. J Fish Res Bd Canada 25: 49–70.ML DahlbergDL ShumwayDoudorofP1968Influence of dissolved oxygen and carbon dioxide on swimming performance of largemouth bass and coho salmon.J Fish Res Bd Canada254970
- 61. Warren CE, Doudoroff P, Shumway DL (1973) Development of dissolved oxygen criteria for freshwater fish. US Environmental Protection Agency, Ecological Research Series Report EPA-R3-73-019 Washington, DC.121.CE WarrenP. DoudoroffDL Shumway1973Development of dissolved oxygen criteria for freshwater fish. US Environmental Protection Agency, Ecological Research Series Report EPA-R3-73-019 Washington, DC.121
- 62. Roby DD, Lyons DE, Craig DP, Collis K, Visser GH (2003) Quantifying the effect of predators on endangered species using a bioenergetics approach: Caspian terns and juvenile salmonids in the Columbia River estuary. Can J Zool 81: 250–265.DD RobyDE LyonsDP CraigK. CollisGH Visser2003Quantifying the effect of predators on endangered species using a bioenergetics approach: Caspian terns and juvenile salmonids in the Columbia River estuary.Can J Zool81250265
- 63. Ryan BA, Smith SG, Butzerin JM, Ferguson JW (2003) Relative vulnerability to avian predation of juvenile salmonids tagged with passive integrated transponders in the Columbia River estuary, 1998–2000. Trans Am Fish Soc 132: 275–288.BA RyanSG SmithJM ButzerinJW Ferguson2003Relative vulnerability to avian predation of juvenile salmonids tagged with passive integrated transponders in the Columbia River estuary, 1998–2000.Trans Am Fish Soc132275288
- 64. Järvi T (1989) Synergistic effect on mortality in Atlantic salmon, Salmo salar, smolt caused by osmotic stress and presence of predators. Environ Biol Fishes 26: 149–152.T. Järvi1989Synergistic effect on mortality in Atlantic salmon, Salmo salar, smolt caused by osmotic stress and presence of predators.Environ Biol Fishes26149152
- 65. Mesa MG (1994) Effects of multiple acute stressors on the predator avoidance ability and physiology of juvenile Chinook salmon. Trans Am Fish Soc 123: 786–793.MG Mesa1994Effects of multiple acute stressors on the predator avoidance ability and physiology of juvenile Chinook salmon.Trans Am Fish Soc123786793
- 66. Armstrong DA, Rooper C, Gunderson D (2003) Estuarine production of juvenile Dungeness crab (Cancer magister) and contribution to the Oregon-Washington coastal fishery. Est Coasts 26: 1174–1188.DA ArmstrongC. RooperD. Gunderson2003Estuarine production of juvenile Dungeness crab (Cancer magister) and contribution to the Oregon-Washington coastal fishery.Est Coasts2611741188
- 67. Bernatis JL, Gerstenberger SL, McGaw IJ (2007) Behavioral responses of the Dungeness crab, Cancer magister, during feeding and digestion in hypoxic conditions. Mar Biol 150: 941–951.JL BernatisSL GerstenbergerIJ McGaw2007Behavioral responses of the Dungeness crab, Cancer magister, during feeding and digestion in hypoxic conditions.Mar Biol150941951
- 68. Stone RP, O'Clair CE (2001) Seasonal movements and distribution of Dungeness crabs Cancer magister in a glaciated southeastern Alaska estuary. Mar Ecol Prog Ser 214: 167–176.RP StoneCE O'Clair2001Seasonal movements and distribution of Dungeness crabs Cancer magister in a glaciated southeastern Alaska estuary.Mar Ecol Prog Ser214167176
- 69. McGaw IJ, Reiber CL, Guadagnoli JA (1999) Behavioral physiology of four crab species in low salinity. Biol Bull 196: 163–176.IJ McGawCL ReiberJA Guadagnoli1999Behavioral physiology of four crab species in low salinity.Biol Bull196163176
- 70. Sugerman PC, Pearson WH, Woodruff DL (1983) Salinity detection and associated behavior in the Dungeness crab, Cancer magister. Estuaries 6: 380–386.PC SugermanWH PearsonDL Woodruff1983Salinity detection and associated behavior in the Dungeness crab, Cancer magister.Estuaries6380386
- 71. Curtis DL, Vanier CH, McGaw IJ (2010) The effects of starvation and acute low salinity exposure on food intake in the Dungeness crab, Cancer magister. Mar Biol 157: 603–612.DL CurtisCH VanierIJ McGaw2010The effects of starvation and acute low salinity exposure on food intake in the Dungeness crab, Cancer magister.Mar Biol157603612
- 72. Seitz RD, Marshall LS Jr, Hines AH, Clark KL (2003) Effects of hypoxia on predator-prey dynamics of the blue crab Callinecties sapidus and the Baltic clam Macoma balthica in Chesapeake Bay. Mar Ecol Prog Ser 257: 179–188.RD SeitzLS Marshall JrAH HinesKL Clark2003Effects of hypoxia on predator-prey dynamics of the blue crab Callinecties sapidus and the Baltic clam Macoma balthica in Chesapeake Bay.Mar Ecol Prog Ser257179188
- 73. Roegner GC, Armstrong D, Shanks A (2007) Wind and tidal influences on crab recruitment to an Oregon estuary. Mar Ecol Prog Ser 351: 177–188.GC RoegnerD. ArmstrongA. Shanks2007Wind and tidal influences on crab recruitment to an Oregon estuary.Mar Ecol Prog Ser351177188
- 74. Vargo SL, Sastry AN (1977) Acute temperature and low dissolved oxygen tolerances of brachyuran crab (Cancer irroratus) larvae. Mar Biol 40: 165–171.SL VargoAN Sastry1977Acute temperature and low dissolved oxygen tolerances of brachyuran crab (Cancer irroratus) larvae.Mar Biol40165171
- 75. Whitney , FA , Freeland HJ, Robert M (2007) Persistently declining oxygen levels in the interior waters of the eastern Pacific. Prog Oceanogr 75: 179–199.WhitneyFAHJ FreelandM. Robert2007Persistently declining oxygen levels in the interior waters of the eastern Pacific.Prog Oceanogr75179199
- 76. Bograd SJ, Castro CG, Di Lorenzo E, Palacios DM, Bailey H, et al. (2008) Oxygen declines and the shoaling of the hypoxic boundary in the California Current. Geophys Res Let 35: L12607.SJ BogradCG CastroE. Di LorenzoDM PalaciosH. Bailey2008Oxygen declines and the shoaling of the hypoxic boundary in the California Current.Geophys Res Let35L12607
- 77. Stramma L, Schmidko S, Levin LA, Johnson GC (2010) Ocean oxygen minima expansions and their biological impacts. Deep-Sea Res I, : L. StrammaS. SchmidkoLA LevinGC Johnson2010Ocean oxygen minima expansions and their biological impacts.Deep-Sea ResI,
- 78. Keeling RF, Garcia HE (2002) The change in oceanic O2 inventory associated with recent global warming. Proc Natl Acad Sci. RF KeelingHE Garcia2002The change in oceanic O2 inventory associated with recent global warming.Proc Natl Acad Sci
- 79. Bricker S, Longstaff B, Dennison W, Jones A, Boicourt K, et al. (2007) Effects of Nutrient Enrichment in the Nation's Estuaries: A Decade of Change. NOAA Coastal Ocean Program Decision Analysis Series No. 26. National Centers for Coastal Ocean Science, Silver Spring, MD. 328 p.S. BrickerB. LongstaffW. DennisonA. JonesK. Boicourt2007Effects of Nutrient Enrichment in the Nation's Estuaries: A Decade of Change.NOAA Coastal Ocean Program Decision Analysis Series No. 26. National Centers for Coastal Ocean Science, Silver Spring, MD328
- 80. Hauri C, Gruber N, Plattner GK, Alin S, Feely RA, et al. (2009) Ocean acidification in the California Current System. Oceanogr 22: 60–71.C. HauriN. GruberGK PlattnerS. AlinRA Feely2009Ocean acidification in the California Current System.Oceanogr226071