The water quality of the Klamath River has gained the attention of many agencies and organizations. Much of this attention is due to the poor water quality of Upper Klamath Lake from which the Klamath River flows (Figure 1). Upper Klamath Lake is a large shallow lake that has been classified as hyper-eutrophic (Vincent 1968) in which massive near-monoculture blooms of the blue-green algae Aphanizomenon flosaquae occur annually. This abundant algal production causes high pH and dissolved oxygen swings from supersaturation to depletion as well as other problems (USGS 1993). The Oregon Department of Environmental Quality has listed several reaches of the Klamath River on the 303(d)(1) list of water quality limited water bodies. Certain reaches of the river downstream of Upper Klamath Lake can be water quality limited during dry, warm seasonal periods when water temperatures are greater than 20°C, dissolved oxygen fluctuates widely with minimums of near 6 mg/L or less and pH levels reach approximately 10.0 units.
The most common cause for increased algal biomass in lakes is an increase in nitrogen and phosphorous (Wetzel 1983 as cited in USGS 1993). The addition of these nutrients to the Klamath River system, and to Upper Klamath Lake in particular, can be attributed to many activities. The most important of these likely include agricultural run-off (43-79percent of all incoming nutrients to the lake (USGS 1993)), conversion of marsh to agricultural land (USGS 1993) and low water levels in Upper Klamath Lake (Kann 1995).
Poor water quality, loss of habitat and many other conditions in Upper Klamath Lake have been attributed to the decline of the Lost River sucker (Deltistes luxatus) and shortnose sucker (Chasmistes brevirostris). In 1988, a determination was made by the U.S. Fish and Wildlife Service to list the two species as endangered (Federal Register 53:27130-27134).
Trout make up a small proportion of fish in the lake. Critically warm water temperatures typically cause the fish to migrate to tributary mouths and springs in the lake.
In 1994 PacifiCorp initiated a periodic water quality monitoring program in the vicinity of its Klamath River hydroelectric projects. Additionally, PacifiCorp participates in a cooperative water temperature study directed by the Karuk Tribe.
The objective of this report is to present the water quality data collected in 1994 and 1995 as part of PacifiCorp’s monitoring program. The primary emphasis of this monitoring is to help characterize baseline water quality conditions in the project areas. Analysis of the data includes general longitudinal trends in water quality and comparison to Oregon and California state water quality standards. This document will be updated annually and all data are available to cooperators and interested parties upon request. Future monitoring objectives are described in section 6.0.
Originating in southern Oregon, the Klamath River flows southwesterly approximately 287 miles (459.2 km) through Oregon and California to the Pacific Ocean. Most of the upper tributaries to the basin drain into Upper Klamath Lake located from river mile (RM) 279 to 254.3. With lake elevation controlled by Link River dam, flow into the Klamath River is managed by lake elevations, irrigation demands, and instream flow requirements below Iron Gate dam at RM 190.
Upper Klamath Lake provides valuable habitat for the endangered Lost River and Shortnose suckers as does other segments of the Klamath River upstream of Iron Gate dam. Resident salmonids, mostly rainbow trout (Oncorynchus mykiss), are found throughout the basin. Chinook (O. tshawyscha) and coho (O. kisutch) salmon, along with steelhead (O. mykiss), lamprey (Lampetra) and many other fish species are present from Iron Gate dam downstream to the ocean.
Within the upper Klamath River basin, defined here as RM 190 to headwater, PacifiCorp owns and operates 6 hydroelectric projects (Figure 1). Five of the projects are located on the Klamath River and one is on Fall Creek, a tributary to the mainstem. PacifiCorp also owns and operates Keno dam (RM 230), a non-hydroelectric reregulating facility located on the Klamath River. The Eastside project is the most upstream project (RM 253.7) located within the city limits of Klamath Falls, Oregon. The Iron Gate project is furthest downstream (RM 190).
The Link River dam (RM 254) provides regulation of Upper Klamath Lake elevation, diverts water to the Eastside and Westside powerhouses and maintains a minimum flow in the Link River reach between the dam and Eastside powerhouse. Keno dam (RM 230) is operated as a reregulating facility (as mentioned above) to control Lake Ewauna levels, J.C. Boyle inflows and minimum flow requirements below Iron Gate dam. J.C. Boyle (RM 225) consists of a dam, diversion canal (and associated bypass reach), and a powerhouse. The powerhouse typically operates as a "peaking" facility. Copco No. 1 (RM 199) operates for power generation, flood control, and Copco and Iron Gate reservoir water surface elevation control. The Copco No. 1 powerhouse is located at Copco dam. Copco No. 1 (RM 198) consists of a diversion dam, flowline, and powerhouse (located 1.4 RM downstream of Copco No. 2 dam). Copco No. 2 is entirely dependant upon Copco No. 1 for water with which to generate and functions as a slave to Copco No. 1. Iron Gate dam serves as the downstream most reregulating point on the system. The powerhouse is located at the dam.
Eighteen sites were monitored for water quality (Table 1). At eight sites, PacifiCorp attempted to monitor water temperature continuously using Ryan TempMentor® and Hobo® digital thermographs. At most sites the thermographs recorded hourly water temperature and were downloaded every other month. Water temperature data collected from the Westside Powerhouse, Keno Tailrace, and Copco No. 2 Powerhouse sites was provided to the Karuk Tribe of California as part of a cooperative effort to monitor water temperatures in the Klamath River mainstem. Continuity of data collection at monitoring sites varied due to a variety of reasons such as malfunctioning or loss of the thermographs. The Keno Tailrace thermograph was removed per instruction by the Karuk Tribe on October 20, 1995. PacifiCorp reestablished this site in June, 1996.
|
Site Description |
River Mile |
Approx Elev-ation |
Periodic Water Quality Monitoring |
Periodic Water Quality Monitoring |
Periodic TDG Monitoring |
Periodic TDG Monitoring |
Continuous Temperature Monitoring |
Continuous Temperature Monitoring |
|
1994 |
1995 |
1994 |
1995 |
1994 |
1995 |
|
Link River Dam |
254.3 |
4146 |
! |
! |
! |
|
Eastside Powerhouse Tailrace |
253.7 |
4085 |
! |
! |
! |
|
Westside Powerhouse Tailrace |
253.3 |
4080 |
! so |
! |
! so |
|
Keno Dam Tailrace |
230.0 |
4060 |
! |
! |
! |
! |
|
J.C. Boyle Reservoir Inflow |
228.0 |
3800 |
! |
! |
! |
! |
! |
|
Spencer Creek |
! |
! |
! |
|
Top of J.C. Boyle Bypass Reach |
224.5 |
3720 |
! |
! |
! |
! |
! |
! wo |
|
Bottom of J.C. Boyle Bypass Reach |
220.4 |
3335 |
! |
! |
! |
! |
! |
|
J.C. Boyle Powerhouse Tailrace |
220.4 |
3330 |
! |
! |
! |
! |
|
Downstream of J.C. Boyle Powerhouse |
220.2 |
3320 |
! |
! |
|
Shovel Creek |
! |
! |
! wo |
|
Copco Reservoir Inflow |
205.5 |
2625 |
! |
! |
! |
|
Copco No. 1 Powerhouse Tailrace |
198.6 |
2485 |
! so |
! |
! |
! |
|
Copco No. 2 Powerhouse Tailrace |
196.9 |
2322 |
! |
! |
! |
! |
! so |
! wo |
|
Fall Creek |
2485 |
! |
! |
! |
! |
|
Jenny Creek |
! |
! wo |
|
Iron Gate Powerhouse Tailrace |
190.1 |
2169 |
! |
! |
! |
! |
|
Bogus Creek |
2150 |
! |
! wo |
! so |
! so |
so=data available for summer season only
wo=data availble for winter season only
Table 1. Available data for PacifiCorps Klamath River area water quality monitoring sites
Water quality was monitored at PacifiCorp’s sites five times in 1994 and also in 1995 (March, May, July, August, and October, 1995/November 1994). Due to the limited scope of this data, the results presented here are not intended to provide a complete picture of the system dynamics. For example, this data does not reveal diurnal fluctuation; some variance within the data may occur within each water quality variable since the data was not collected at a consistent time of day.
Dissolved oxygen (DO)(mg/L), pH, conductivity (umhos), and Total Dissolved Gas (TDG)(percent saturation) were measured at 17 sites. With the exception of TDG, water quality variables were monitored with a Hydrolab® Surveyor II. A Model TB-F Total Dissolved Gas Monitor manufactured by Common Sensing Inc.® was used to record TDG and the following parameters: barometric pressure, water temperature, atmospheric pressure at the sensor (Pt), and the difference between barometric pressure and atmospheric pressure (DP). The Surveyor II was calibrated prior to and following each monitoring trip and the TDG meter was checked periodically for 100 percent saturation in air with a dry probe; data was adjusted according to post-calibration values. If pre and post calibration values for DO and pH were beyond one unit of synchronicity, the data was disregarded. For this reason and malfunctioning of equipment, etc. there are gaps and inconsistencies in the collection of periodic water quality sampling. Data gaps in TDG monitoring may also occur if the hydro project was not operational at the time of sampling.
All measurements were taken from approximately the same location on shore at each sampling site. The instruments (including thermographs) were placed in the main flow of the river/stream or in an area of thorough mixing.
The data presented in this report were summarized and graphed using EXCEL 5.0 software. PacifiCorp’s sampling locations and the type of sampling that occurred at each location is shown in Table 1.
Since the Klamath River begins at Upper Klamath Lake the water quality of the lake greatly influences water quality of the river (downstream of the lake). A critically dry year (when lake levels are low during the early part of the year) occurred in 1994, whereas 1995 is considered a somewhat average to wet year (when lake levels are higher). The average flows per month in 1994 and 1995 at Link River dam, J.C. Boyle powerhouse and Iron Gate dam are presented in Figure 2. The Klamath River flow downstream of Link River dam is derived from USGS gage No. 11507500 plus flow through the Westside powerhouse. The flow downstream of J.C. Boyle dam was recorded at USGS gage No. 11510700. At Iron Gate dam, the flow was measured at USGS gage No. 11516530 approximately 0.25 miles downstream. In March, April and May the flows in 1995 were roughly 4.5 times greater than in 1994.
In 1994 maximum and minimum DO concentrations at all mainstem stations ranged from a high of 13.16 mg/L at Iron Gate on March 15 to a low of 6.22 mg/L at Westside tailrace on August 23 (Figures 2-3). In 1995 maximum and minimum concentrations ranged from a high of 11.70 mg/L at Copco No. 1nflow on March 6, to a low of 5.94 mg/L at Keno dam on July 19 (Figures 4-5). In 1994 DO concentrations in monitored tributaries to the Klamath River ranged from a high of 11.94 mg/L on November 15 at Shovel Creek to a low of 10.21 mg/L on May 20 at Fall Creek (Figure 6). In 1995 tributary DO concentrations ranged from 13.43 mg/L on March 6 to 7.9 mg/L on July 19 at Jenny Creek (Figure 7).
The state of Oregon Department of Environmental Quality (ODEQ) regulations relating to water quality control (ODEQ 1992) specify that DO in the Klamath River from Upper Klamath Lake to Keno dam shall not be less than 5 mg/L and that from Keno dam to the California border shall not be less than 7 mg/L. In 1995 DO concentrations were less than these standards at the top of J.C. Boyle bypass on August 29 (6.25 mg/L) and on July 19 in the J.C. Boyle tailrace (6.54 mg/L).
Water Quality objectives in the State of California North Coast Region of the Water Quality Control Board (CA-WQCB 1994) specify that the Klamath River in California shall not be less than 7.0 mg/L. Dissolved oxygen concentrations observed which were less than this standard occurred in the Copco No. 2 tailrace on August 24, 1994 (6.94 mg/L) and on July 19, 1995 (6.42 mg/L).
DO concentrations in 1994 and 1995 do not appear to vary despite the flow regimes. DO concentrations were noted which were less than state standards but minimum values did not reach levels considered critically low for salmonids (5.0 mg/L or less). The lowest DO concentrations occurred in late summer in both years; this likely corresponds to algal die offs in Upper Klamath Lake and mainstem reservoirs creating high biological oxygen demand.
In 1994 mainstem pH concentrations ranged from a high of 9.77 on July 11 to a low of 7.02 on March 14 at Eastside (Figures 8-9). In 1995 mainstem concentrations ranged from 9.69 at Link River dam to 7.30 at J.C. Boyle tailrace on July 19 (Figures 10-11). pH concentrations in tributaries to the Klamath in 1994 ranged from 8.2 on August 24 at Fall Creek to 7.51 on September 29 at Shovel Creek (Figure 12). In 1995 pH concentrations in tributaries ranged from 8.33 at Jenny Creek on August 28 to 7.42 at Shovel Creek on July 18 (Figure 13).
ODEQ water quality control regulations specify that pH concentrations shall remain between 7.0 and 9.0. On July 11, 1994, pH concentrations on the mainstem were greater than 9.0 at three sites: Keno dam, Westside and Eastside (9.07, 9.73 and 9.77 respectively). In 1995, the upper pH limit was exceeded seven times: Link River dam on July 19, August 30 and October 19 (9.69, 9.64, 9.13 respectively), two at Westside on August 30 and October 19 (9.52 and 9.13) and two at Eastside on July 19 and August 30 (9.68 and 9.68). pH values in Spencer Creek remained within these limits in 1995.
Figure 2. 1994 dissolved oxygen (mg/L) data in the Klamath River mainstem in Oregon.
Figure 3. 1994 dissolved oxygen (mg/L) data on the Klamath River mainstem in California
Figure 4. 1995 dissolved oxygen (mg/L) data on the Klamath River mainstem in Oregon
Figure 5. 1995 dissolved oxygen (mg/L) data on the Klamath River mainstem in California
Figure 6. 1994 dissolved oxygen (mg/L) levels in the Klamath River tributaries
Figure 7. 1995 dissolved oxygen (mg/L) data on the Klamath River tributaries
Figure 8. 1994 pH values on the Klamath River mainstem in Oregon.
Figure 9. 1994 pH values on the Klamath River mainstem in California
Figure 10. 1995 pH values on the Klamath River mainstem in Oregon.
Figure 11. 1995 pH values on the Klamath River mainstem in California.
Figure 12. 1994 pH values on the Klamath River tributaries.
Figure 13. 1995 pH values on the Klamath River tributaries
CA-WQCB standards specify that pH concentrations on the Klamath River mainstem shall remain between 7.0 and 8.5. The upper standard was exceeded on the mainstem twice in 1994 and three times in 1995. In 1994, the standard was exceeded at Iron Gate dam on August 24 (8.54) and at Copco No. 1 tailrace on July 12 (8.51). In 1995, the standard was exceeded at Iron Gate on September 29 (8.72), and at Copco No. 1 tailrace on July 12 (8.89) and Copco No. 1nflow on May 20 (9.31). pH values at the California tributary sites remained within these limits in 1994 and 1995.
The number of times that values were observed outside the state standards in 1995 was double that in 1994. Most of these instances occurred at the three sampling sites associated with Upper Klamath Lake (Link River dam, Westside and Eastside). As previously mentioned, Upper Klamath Lake is a large, shallow, hyper-eutrophic lake in which large near-monoculture blooms of blue-green algae occur annually. High pH values are frequently associated with algal blooms. Although lacking refutable evidence, it is possible that early and/or large algal blooms are associated with low lake levels in the spring. pH levels in the Klamath River were higher over a similar sampling period in 1995 than in 1994 even though lake levels were higher in 1995. An investigation conducted by the U.S.G.S. concluded that more variability in water quality can be explained by climatic variables than by lake level (U.S.G.S. 1995). As expected, research by the Klamath Tribe indicated that median chlorophyll-a concentrations in Upper Klamath Lake were high in June, 1995 (200 ug/L as opposed to 1994 when it was approximately 130 mg/L)(Kann, 1995).
In 1994 mainstem values ranged from 95.1percent at Copco No. 1 tailrace on November 15 to 115.1percent at Iron Gate on July 12 (Figures 14-15) and 99.6percent to 102.5percent at Fall Creek on November 15 and May 20, respectively in the tributaries (Figure 16). Mainstem values in 1995 ranged from 97.1percent on October 18 at Copco No. 1 tailrace to 106.8percent on October 19 at Westside (Figures 17-18) and 99.6percent on October 19 to 100.6percent on May 2 at Fall Creek in the tributaries (Figure 19).
ODEQ standards specify that nitrogen saturation shall not exceed 110percent in waters greater than two feet in depth or 105percent in waters less than two feet in depth. These values were not exceeded in 1994 or 1995 at any of the sampling sites on any of the days sampling occurred. CA-WQCB does not yet have a standard for this parameter but on two occasions in 1994, TDG at Iron Gate dam was 115.1 percent on July 12 and 111.4 percent on August 24.
These relatively high saturation levels in 1994 are likely associated with the flow regimes during this critically dry water year. During those sampling periods, the generators in the powerhouses were not operating efficiently due to lower river flows. To prevent cavitation of the turbine and possible damage, large amounts of air are mixed with the water as it passes through the turbines. This mixing can result in a higher saturation of TDG in the water.
Figure 14. 1994 total dissolved gas (% saturation) data on the Klamath River mainstem in Oregon.
Figure 15. 1994 total dissolved gas (% saturation) data on the Klamath River mainstem in California.
Figure 16. 1994 total dissolved gas (% saturation) data on the Klamath River tributaries
Figure 17. 1995 total dissolved gas (% saturation) data on the Klamath River mainstem in Oregon.
Figure 18. 1995 total dissolved gas (% saturation) data on the Klamath River mainstem in California.
Figure 19. 1995 total dissolved gas (% saturation) data in the Klamath River tributaries.
High saturation levels at Iron Gate dam do not adversely affect fish at the Iron Gate Fish Hatchery (in the form of gas bubble disease) since the water intake for the hatchery is above the powerhouse. Furthermore, this water passes through an aeration tower prior to reaching the hatchery which would likely dissipate any supersaturated nitrogen in the water. TDG in the Klamath River is likely to be dissipated considerably as it passes over a series of riffles located approximately 100m downstream of Iron Gate dam.
In 1994 specific conductivity values ranged from 456 umhos/cm at J.C. Boyle Inflow on March 14 to 113 umhos/cm at Link River dam on the same date (Figure 20-21). Specific conductivity values in the tributaries ranged from 117 umhos/cm at Shovel Creek on November 15 to 154 umhos/cm Fall Creek on September 29 (Figure 22). In 1995 specific conductivity ranged from 429 umhos at J.C. Boyle Tailrace on March 6 to 101 umhos at Link River dam on October 19 (Figure 23-24). Specific conductivity in the tributaries ranged from 53 umhos in Spencer Creek on May 3 to 212 umhos in Bogus Creek on August 28 (Figure 25).
Figure 20. 1994 specific conductivity (uS/cm) on the Klamath River mainstem in Oregon.
Figure 21. 1994 specific conductivity (uS/cm) on the Klamath River mainstem in California.
Figure 22. 1994 specific conductivity (uS/cm) on the Klamath River tributaries
Figure 23. 1995 specific conductivity (uS/cm) on the Klamath River mainstem in Oregon
Figure 24. 1995 specific conductivity (uS/cm) on the Klamath River mainstem in California.
Figure 25. 1995 specific conductivity (uS/cm) on the Klamath River tributaries.
ODEQ standards state that specific conductivity shall not exceed 400 umhos. These standards were exceeded three times in 1994 on March 14 at Keno dam (454 umhos), J.C. Boyle Inflow (456 umhos) and at the top of the J.C. Boyle Bypass (436 umhos). In 1995 the standards were exceeded twice on March 7 at the top of J.C. Boyle Bypass (421 umhos) and in the tailrace of J.C. Boyle dam (429 umhos).
CA-WQCB standards specify that specific conductivity on the Klamath River mainstem from the OR-CA border to Iron Gate reservoir shall not exceed 275 umhos in 50percent of measurements taken and that 90percent of measurements taken shall not exceed 425 umhos. Below Iron Gate reservoir the standards state that 50percent of measurements taken shall not exceed 275, and 90percent shall not exceed 350 umhos. These standards were not exceeded in 1994 or 1995.
All measurements greater than state standards were collected in the spring of 1994. Since specific conductivity is a measure of ionized or dissolved minerals in the water, it is expected that conductivity would increase as water leaches through agricultural soils and into the river. Such action is generally higher during spring thaws and run-off. Furthermore, since 1994 was a critically low water year, conductivity would be expected to increase since less than normal river flow was available to dilute the ionized and dissolved minerals.
In 1994 the water temperature range on the mainstem Klamath River was from approximately 2°C at several sampling sites in late November and late December to approximately 25°C in mid to late July at several sites (Figures 26-30). In 1995 water temperatures on the mainstem of the Klamath ranged from approximately 2.5°C in January at several sites to nearly 25°C at Keno dam in mid-June (Figures 31-35). On Bogus Creek in 1994 water temperatures ranged from approximately 2.0°C on November 15 to 28°C on July 24 and in 1995 from approximately 2.5°C in mid-February to a high of approximately 22°C in late June and late July (Figures 36-37).
Figure 26. 1994 daily maximum and minimum water temperatures of the Klamath River as measured at Westside powerhouse.
Figure 27. 1994 daily maximum and minimum water temperatures of the Klamath River as measured at the Keno dam tailrace.
Figure 28. 1994 daily maximum and minimum water temperatures of the Klamath River as measured at the top of J.C. Boyle dam.
Figure 29. Boyle Bypass 1994 temps
Figure 30. 1994 daily maximum and minimum water termperatures on the Klamath River as measured at Copco No. 2 tailrace.
Figure 31. 1995 daily maximum and minimum water termperatures on the Klamath River as measured at Westside powerhouse.
Figure 32. 1995 daily maximum and minimum water termperatures on the Klamath River as measured at Keno tailrace.
Figure 33. 1995 daily maximum and minimum water termperatures on the Klamath River as measured at the top of J. C. Boyle bypass reach.
Figure 34. 1995 daily maximum and minimum water temperatures of the Klamath River as measured at the bottom of J.C. Boyle bypass reach.
Figure 35. 1995 daily maximum and minimum water termperatures on the Klamath River as measured at Copco No. 2 tailrace.
Figure 36. 1994 daily maximum and minimum water termperatures of Bogus creek.
Figure 37. 1995 daily maximum and minimum water termperatures of Bogus Creek.
Due to large gaps in the thermograph data, it is difficult to make generalizations with regard to water temperature in 1994 and 1995. However, where data was collected during the summer months, all sites except the bottom of the bypass reach at J.C. Boyle had maximum water temperatures above 20°C which is generally considered the thermal maximum for salmonids beyond which acute stress occurs. Water temperatures at the bottom of the bypass reach at J.C. Boyle did not reach 20°C. This is likely due to the strong influence of springs in this area. These springs can make up to 75percent of the flow during normal flow operation. Salmonids may seek these areas and tributaries to the Klamath River such as Spencer Creek, Shovel Creek, Fall Creek and Jenny Creek as cold water refugia.
In 1994 four sites as opposed to two in 1995 had both daily minimum and maximum water temperatures exceeding 20°C for at least four weeks in the summer. These locations were Westside, Keno Tailrace, Top of J.C. Boyle bypass reach, and Copco No. 2 tailrace in 1994. In 1995 daily minimum and maximum water temperatures which exceeded 20°C occurred at Westside and Keno Tailrace. Generally such conditions occurred in late June to early July and lasted until mid-to late-August.
In an effort to depict annual seasonal variation at individual sites the data were gathered for each site and averaged over the summer months (May - October) for each year and compared for longitudinal trends. Sufficient data was not available to compare winter months in a similar manner (Figures 38-41).
Figure 38. Mean summer and winter dissolved oxygen values on the Klamath River in 1994 and 1995.
Figure 39. Mean summer and winter pH values on the Klamath River in 1994 and 1995.
Figure 40. Mean summer and winter total dissolved gas values on the Klamath River in 1994 and 1995.
Figure 41. Mean summer and winter conductivity values on the Klamath River in 1994 and 1995.
There was no clear pattern between mean dissolved oxygen values in the summer of 1994 and summer 1995 despite the high and low flow water years. Some variation in the data may be due to the time of day in which samples were collected since dissolved oxygen data generally show large diel fluctuations. Dissolved oxygen values were only slightly higher (approximately 0.5 mg/L) in Upper Klamath Lake in 1995 than in 1994. DO was considerably higher 1994 than in 1995 at the bottom of the J.C. Boyle bypass reach and at Copco No. 1 inflow. This is likely due to the greater influence that the natural springs had upon the total flow in the criticial dry year of 1994. (The tailrace is downstream of the springs.) It is difficult to determine as to why DO differences are so great between years in Copco No. 1 tailrace.
As with the DO data, no clear pattern was evident between years for mean pH values but varied between years in much the same way as DO. Again, this variation may be due to the time of day that samples were collected since pH also fluctuates a great deal throughout the day.
Total dissolved gas saturation fluctuated very little between years. The only variation occurred at Iron Gate dam when TDG levels were higher in 1994 than in 1995.
Specific conductance fluctuated in the same way from site to site between years. As expected, specific conductance was higher in 1994 than in 1995 since concentrations of ionized and dissolved minerals would be higher in lower volumes of water i.e., during low flow years.
In the summer of 1996 a more comprehensive study will begin to evaluate water quality throughout the entire Klamath basin in cooperation with numerous entities including federal agencies, Oregon and California state departments, universities and tribes. This study will attempt to fill data gaps such that a computer generated water quality model can be developed for the basin and hence a more complete picture of the seasonal water quality dynamics in the system. In doing so, PacifiCorp will continue to monitor water quality and continuous water temperature data as in the past. In addition, PacifiCorp will monitor monthly profiles in Copco and Iron Gate reservoirs (May through October) and coordinate efforts with the other parties involved to collect various nutrient samples and continuous water temperature profiles in Iron Gate reservoir.
There is a general belief among scientists that higher flows will result in improved water quality. The data gathered and presented here do not unequivocally support that higher flows will result in improved water quality. For example, there were more instances when water quality standards did not meet Oregon/California state standards in 1995 (higher flow/wet water year) than in 1994 (lower flow/dry water year). However, flows in 1995 were only significantly greater than flows in 1994 during the spring months when water quality is not usually limited. Furthermore, the quantity of data and the consistency at which the data was collected are likely not sufficient to make such conclusions. The 1996 investigation may provide the evidence needed to correlate water quality and stream flow.
It is clear that as the water quality conditions in Upper Klamath Lake worsen, so does the water quality of the Klamath River up to the natural spring inflow below J.C. Boyle dam. Conditions improve to some degree depending on the relative contribution that the springs make to overall river flow.
Water quality parameters and continuous water temperature data will continue to be collected as it was in 1994 and 1995 and data collection efforts will be expanded in 1996.
California North Coast Regional Water Quality Control Board, 1994. Water quality Control Plan for the North Coast Region. Santa Rosa, CA.
Kann, J. 1995. Effects of lake level management on water quality in Upper Klamath Lake, Oregon. Klamath Tribes Natural Resources. Chiloquin, OR.
Oregon Department of Environmental Quality, 1992. Oregon administrative rules Chapter 340, Regulations relating to: Water quality control. Portland, OR.
U.S. Geological Survey, 1993. A review of possible causes of nutrient enrichment and decline of endangered sucker populations in Upper Klamath Lake, Oregon. Water-Resources Investigations Report 93-4087. Portland, OR.
U.S. Geological Survey, 1995 (in preparation). Relations between selected water quality constituents and lake stage in Upper Klamath and Agency Lakes, Oregon. Portland, OR.
Vincent, D.T. 1968. The influences of some environmental factors on the distribution of fishes in Upper Klamath Lake. M.S. Thesis, Oregon State University, Corvallis.
Wetzel, R.G. 1983. Limnology: (2d ed.), Saunders College Publishing, Philadelphia.
